[Federal Register Volume 80, Number 191 (Friday, October 2, 2015)]
[Rules and Regulations]
[Pages 59976-60021]
From the Federal Register Online via the Government Publishing Office [www.gpo.gov]
[FR Doc No: 2015-24820]



[[Page 59975]]

Vol. 80

Friday,

No. 191

October 2, 2015

Part IV





 Department of the Interior





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Fish and Wildlife Service





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50 CFR Part 17





Endangered and Threatened Wildlife and Plants; Two Foreign Macaw 
Species; Final Rule

  Federal Register / Vol. 80 , No. 191 / Friday, October 2, 2015 / 
Rules and Regulations  

[[Page 59976]]


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DEPARTMENT OF THE INTERIOR

Fish and Wildlife Service

50 CFR Part 17

[Docket No. FWS-R9-ES-2011-0101; 450 003 0115]
RIN 1018-AY33


Endangered and Threatened Wildlife and Plants; Two Foreign Macaw 
Species

AGENCY: Fish and Wildlife Service, Interior.

ACTION: Final rule.

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SUMMARY: We, the U.S. Fish and Wildlife Service (Service), are listing 
the military macaw (Ara militaris) and the great green macaw (Ara 
ambiguus) as endangered under the Endangered Species Act of 1973, as 
amended (ESA). These species are both endemic to Central and South 
America. Despite conservation efforts, these species' populations are 
in decline, primarily due to habitat loss, fragmentation, and 
degradation; small population size; poaching; and regulatory mechanisms 
that are inadequate to ameliorate these threats throughout their 
ranges.

DATES: This rule becomes effective November 2, 2015.

ADDRESSES: This final rule is available on the Internet at http://www.regulations.gov and comments and materials received, as well as 
supporting documentation used in the preparation of this rule, will be 
available for public inspection, by appointment, during normal business 
hours at: U.S. Fish and Wildlife Service; 5275 Leesburg Pike, Falls 
Church, VA 22041.

FOR FURTHER INFORMATION CONTACT: Janine Van Norman, Chief, Branch of 
Foreign Species, Endangered Species Program, U.S. Fish and Wildlife 
Service, 5275 Leesburg Pike, Falls Church, VA 22041; telephone 703-358-
2171. If you use a telecommunications device for the deaf (TDD), call 
the Federal Information Relay Service (FIRS) at 800-877-8339.

SUPPLEMENTARY INFORMATION: 

Executive Summary

I. Purpose of the Regulatory Action

    On January 31, 2008, the Service received a petition dated January 
29, 2008, from Friends of Animals, represented by the Environmental Law 
Clinic, University of Denver, Sturm College of Law, requesting that we 
list 14 parrot species under the Endangered Species Act of 1973, as 
amended (ESA or Act; 16 U.S.C. 1531 et seq.). As part of a court-
approved settlement agreement, the Service agreed to submit a 
determination as to whether the petitioned action is warranted, not 
warranted, or warranted but precluded by other listing actions for the 
military macaw (Ara militaris) and the great green macaw (Ara ambiguus) 
to the Federal Register by June 30, 2012. On July 6, 2012, the Service 
published a proposed rule (77 FR 40172) to add the military macaw and 
great green macaw as endangered species to the Federal List of 
Endangered and Threatened Wildlife. This final rule completes the 
listing process for these species.

II. Summary of the Major Provisions of the Regulatory Action

    We are listing the military macaw (Ara militaris) and the great 
green macaw (Ara ambiguus) as endangered species under the Act. We are 
finalizing this action primarily because of the effects of poaching, 
habitat loss, fragmentation, and degradation on their populations; 
their small and declining population sizes; and inadequate regulatory 
mechanisms to ameliorate the threats to the species throughout their 
ranges.
    In this final rule, we used public comments and peer review to 
inform our final determination, as required under the Act. When we 
published the proposed rule on July 6, 2012 (77 FR 40172), we opened a 
60-day comment period on the proposed listing for these species. During 
the comment period, we sought comments from independent specialists 
(peer reviewers) on the specific assumptions and conclusions in our 
listing proposal to ensure that the designation of these species as 
endangered is based on scientifically sound data, assumptions, and 
analyses. In addition, we sought comments from interested parties and 
the public. We considered all comments and information received during 
the comment period. In this final rule, we present and respond to peer 
reviewer and public comments. This rule finalizes the protections 
proposed for these two foreign bird species as endangered species, 
following careful consideration of all comments we received during the 
public comment period.

III. Costs and Benefits

    Section 4(b)(1)(A) of the ESA directs that determinations as to 
whether any species is an endangered or threatened species must be made 
``solely on the basis of the best scientific and commercial data 
available.'' Further, this action is not a ``significant'' regulatory 
action under Executive Order 12866. Therefore, we have not analyzed its 
costs or benefits.

Background

    Section 4(b)(3)(B) of the ESA (16 U.S.C. 1531 et seq.) requires 
that, for any petition to revise the Federal Lists of Endangered and 
Threatened Wildlife and Plants that contains substantial scientific or 
commercial information that listing the species may be warranted, we 
make a finding within 12 months of the date of receipt of the petition 
(``12-month finding''). In this finding, we determine whether the 
petitioned action is: (a) Not warranted, (b) warranted, or (c) 
warranted, but immediate proposal of a regulation implementing the 
petitioned action is precluded by other pending proposals to determine 
whether species are endangered or threatened, and expeditious progress 
is being made to add or remove qualified species from the Federal Lists 
of Endangered and Threatened Wildlife and Plants. Section 4(b)(3)(C) of 
the ESA requires that we treat a petition for which the requested 
action is found to be warranted but precluded as though resubmitted on 
the date of such finding, that is, requiring a subsequent finding to be 
made within 12 months. We must publish these 12-month findings in the 
Federal Register.
    In this document, we announce that listing these two species as 
endangered species is warranted, and we are adding these two species to 
the Federal List of Endangered and Threatened Wildlife in title 50 of 
the Code of Federal Regulations.

Petition History

    On January 31, 2008, the Service received a petition dated January 
29, 2008, from Friends of Animals, as represented by the Environmental 
Law Clinic, University of Denver, Sturm College of Law, requesting that 
we list 14 parrot species under the ESA. The petition clearly 
identified itself as a petition and included the requisite information 
required in the Code of Federal Regulations (50 CFR 424.14(a)). On July 
14, 2009 (74 FR 33957), we published a 90-day finding in which we 
determined that the petition presented substantial scientific and 
commercial information to indicate that listing may be warranted for 12 
of the 14 parrot species.
    In our 90-day finding on this petition, we announced the initiation 
of a status review to list as endangered or threatened under the ESA 
the following 12 parrot species: Blue-headed macaw (Primolius couloni), 
crimson shining parrot (Prosopeia splendens), great green macaw (Ara 
ambiguus), grey-

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cheeked parakeet (Brotogeris pyrrhoptera), hyancith macaw 
(Anodorhynchus hyacinthinus), military macaw (Ara militaris), 
Philippine cockatoo (Cacatua haematuropygia), red-crowned parrot 
(Amazona viridigenalis), scarlet macaw (Ara macao), white cockatoo 
(Cacatua alba), yellow-billed parrot (Amazona collaria), and yellow-
crested cockatoo (Cacatua sulphurea). We initiated the status review to 
determine if listing each of the 12 species is warranted, and initiated 
a 60-day public comment period to allow all interested parties an 
opportunity to provide information on the status of these 12 species of 
parrots. The public comment period closed on September 14, 2009.
    On July 21, 2010, a settlement agreement was approved by the Court 
(CV-10-357, D. DC), in which the Service agreed to submit to the 
Federal Register by July 29, 2011, September 30, 2011, and November 30, 
2011, determinations whether the petitioned action is warranted, not 
warranted, or warranted but precluded by other listing actions for no 
less than 4 of the petitioned species on each date.
    On August 9, 2011, the Service published in the Federal Register a 
12-month status review finding for the crimson shining parrot (a 
finding that listing was not warranted) and a proposed rule for the 
following three parrot species: Philippine cockatoo, white cockatoo, 
and yellow-crested cockatoo (76 FR 49202).
    On October 6, 2011, we published a 12-month status review finding 
for the red-crowned parrot (76 FR 62016); on October 11, 2011, we 
published a 12-month status review and proposed rule for the yellow-
billed parrot (76 FR 62740); and on October 12, 2011, we published a 
12-month status review for the blue-headed macaw and grey-cheeked 
parakeet (76 FR 63480).
    On September 16, 2011, an extension to the settlement agreement was 
approved by the Court (CV-10-357, D. DC), in which the Service agreed 
to submit a determination for the remaining four petitioned species to 
the Federal Register by June 30, 2012.
    On July 6, 2012, the Service published in the Federal Register a 
12-month status review finding and proposed rule for the four following 
parrot species: Great green macaw and the military macaw (77 FR 40172), 
hyacinth macaw (77 FR 39965), and the scarlet macaw (77 FR 40222).
    Upon publication in the Federal Register on July 6, 2012, of the 
12-month status review finding and proposed rule for these species (77 
FR 40172), we initiated a 60-day public comment period, which ended on 
September 4, 2012. Following publication of the proposed rule, we 
implemented the Service's peer review process and during the 60-day 
comment period, solicited scientific and commercial information on the 
species from all interested parties.

Previous Federal Actions

    In our proposed rule, published July 6, 2012 (77 FR 40172), we 
announced that listing the military macaw and the great green macaw as 
endangered was warranted, and we issued a proposed rule to add these 
two species to the Federal List of Endangered and Threatened Wildlife. 
The comment period ended on September 4, 2012; we received 59 comments 
from the public.
    In response to requests received during the public comment period, 
we reopened another public comment period on February 21, 2013, which 
ended on April 22, 2013 (78 FR 12011). During the second comment period 
(see http://www.regulations.gov, docket number FWS-R9-ES-2011-0101), we 
received 25 more comments on these two macaw species and on the 
hyacinth macaw; however, only one submission provided substantive 
information. All comments, including names and addresses of commenters, 
have become part of the administrative record and are available at 
http://www.regulations.gov, docket numbers FWS-R9-ES-2011-0101 and FWS-
R9-ES-2012-0013.

Summary of Comments and Recommendations

    We base this finding on a review of the best scientific and 
commercial information available, including all information received 
during the public comment period. In the September 4, 2012, proposed 
rule, we requested that all interested parties submit information that 
might contribute to development of a final rule. On February 21, 2013, 
we reopened the public comment period where we again requested that all 
interested parties submit information that might contribute to 
development of a final rule. We also contacted appropriate scientific 
experts and organizations and invited them to comment on the proposed 
listings. We received comments from four individuals; one of which was 
from a peer reviewer.

Peer Reviewer Comments

    (1) Comment: One peer reviewer provided information on military 
macaw population surveys confirming the presence of 100 macaws in the 
Tehuacan-Cuicatlan Biosphere Reserve in Mexico.
    Our Response: We have reviewed the additional literature and 
incorporated the new information into our finding. Although the new 
information has been incorporated into the final rule, the new survey 
provided did not change our finding that the military macaw meets the 
definition of an endangered species. The species' overall population 
remains small and fragmented despite additional macaws being observed 
in this one location, and the species is still at risk of extinction 
due to habitat loss, poaching, and small population size.

Public Comments

    (2) Comment: Several commenters expressed concerns about the 
potential impact the listings might have on their business.
    Our Response: We acknowledge that there may be impacts to different 
entities involved in captive breeding of great green and military 
macaws. However, Section 4(b)(1)(A) requires listing decisions to be 
based solely on the best scientific and commercial data available, as 
it relates to the five listing factors in section 4(a)(1) of the Act. 
Therefore, the Service did not consider the impacts on business in its 
listing determination.
    (3) Comment: Some commenters suggest that the Service is using 
outdated information when making the determination for the rule.
    Our Response: The Service is required by the Act to make 
determinations solely on the basis of the best scientific and 
commercial data available. We based the proposed rule on all the 
information we received following the initiation of the 12-month status 
review for the military and great green macaw, as well as all of the 
information we found while conducting our own research. The information 
we use depends on field research and our ability to acquire that 
information. At the time of the publishing of the proposed rule, the 
information we compiled was considered the best available information. 
After publishing the proposed rule, emerging information on the great 
green and military macaw became available. We reviewed that 
information, as well as additional information submitted by the public, 
including more recent information and studies from a species expert and 
conservation organizations within the great green and military macaw's 
range countries. Non-English literature was professionally translated, 
analyzed, and is cited in this document. The information we received 
and subsequently reviewed did not change any of our findings, but 
rather further supported our conclusions. That

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information has been incorporated into this final rule.
    (4) Comment: Some commenters, while not opposed to the listing of 
the species, asked for a special rule under section 4(d) of the Act 
(also called a ``4(d) rule'') that would allow ownership and interstate 
trade of the species to occur without obtaining a permit under the Act.
    Our response: Ownership of a listed species is not prohibited by 
the Act and, therefore, does not require a permit. Because we 
determined that listing the great green and military macaws as 
endangered species under the Act is appropriate, we are not able to 
develop a 4(d) rule for this species. Section 4(d) of the Act allows 
the Service to develop a special rule to apply the prohibitions of 
section 9 or to provide measures that are necessary and advisable to 
provide for the conservation of threatened species only. A special rule 
cannot be promulgated for a species that is listed as endangered under 
the Act. The sale; offer for sale; and delivery, receipt, carrying, 
transport, or shipment in interstate or foreign commerce in the course 
of a commercial activity is prohibited. That said, not all interstate 
trade is prohibited under the ESA. Interstate transfer of animals that 
are not for sale, offered for sale, or in the course of a commercial 
activity is not prohibited.
    We thank all the commenters for their interest in the conservation 
of this species and thank those commenters who provided information for 
our consideration in making this listing determination. Under section 
4(b) of the Act, the Service is required to make listing determinations 
solely on the basis of the best scientific and commercial data 
available after conducting a review of the status of the species. When 
we published our proposed rule, we opened a public comment period 
during which we requested any additional information on the great green 
and military macaw. In making this listing determination, we reviewed 
the best available scientific and commercial information, contacted 
species experts, and searched for the most current information on these 
species with due diligence. Therefore, we have obtained and considered 
the ``best scientific and commercial data available'' in our listing 
determination. After careful consideration, we conclude that these 
species meet the definition of an endangered species under the Act.

Species Information for the Military Macaw

Taxonomy

    The military macaw (Ara militaris, Linnaeus 1766) is in the 
Psittacidae family and is also known as ``guacamaya verde,'' 
``parava,'' and ``ravine parrot.'' Three subspecies of military macaw 
have been proposed and are recognized by some: Ara militaris bolivianus 
(Reichenow 1908), Ara militaris mexicanus (Ridgway 1915), and Ara 
militaris militaris (Linnaeus 1766). Avibase, a database of all birds 
of the world maintained by Bird Studies Canada, and the Integrated 
Taxonomic Information System (ITIS) both recognize subspecies (http://www.itis.gov and http://avibase.bsc-eoc.org/avibase.jsp, accessed 
August 30, 2011). The range of A. m. bolivianus is thought to be in 
Bolivia and northwestern Argentina. The range of A. m. mexicanus is 
thought to be restricted to Mexico.
    Because it is a strong flyer (it has been observed traveling up to 
20 kilometers (km) (12 miles [mi]) per day) and it is a semi-migratory 
species, the physical similarities suggest that seemingly isolated 
populations may be in contact (Juniper and Parr 1998, p. 423), and, 
therefore, their populations may be exchanging genetic material.
    For the purpose of this rule, we are addressing the military macaw 
at the species level. Therefore, we are listing the military macaw 
species as an endangered species, which includes all subspecies.

Description

    The military macaw is an extremely vocal species; it is described 
as being very noisy and is known to shriek (Birdlife International 
(BLI) 2011, p. 1). It is a large macaw (70 centimeters or 27.5 inches 
in length) and is vibrant in color. It has dark lime-green feathers 
mixed with blue flight feathers that are olive-colored underneath. Its 
forehead is red, and it has a bare white facial area and a black bill. 
Its lower back is blue; its tail is red and blue. The southernmost 
population in Bolivia, which extends into Argentina, exhibits reddish 
brown on their throats and cheeks (Juniper and Parr 1998, p. 423). This 
species is often confused with the great green macaw (Ara ambiguus). 
The great green macaw is very similar in appearance to the military 
macaw, but the military macaw has more prominent blue tinge on its hind 
neck, is smaller, and has darker plumage. These two species are 
separated geographically.

Habitat and Life History

    Military macaws nest in tree cavities and cliffs. Cliff-nesting 
parrots, such as the military macaw, also nest colonially (in groups) 
(Bonilla-Ruz et al. 2007a, pp. 730-731). Cliff cavities located in 
ravines used by this species have been documented 25 and 30 meters (m) 
(82 to 98 feet (ft)) above ground (Arcos-Torres and Solano-Ugalde 2008, 
p. 71). Tree cavities used by this species have been observed to be 18 
m (60 ft) above ground and are approximately 75 cm (29.5 inches) deep 
(Baker 1958, p. 98). This species has also been observed to use 
secondary cavities, such as abandoned woodpecker holes, particularly in 
dead pine trees (Strewe and Navarro 2004, p. 50). Military macaws 
alternate nesting and foraging areas based on food availability 
(Bonilla-Ruz 2006, p. 1). Nesting appears to be synchronous with the 
peak fruiting season, which occurs during April and May (Huatatoca 
pers. comm. in Arcos-Torres and Solano-Ugalde 2008, p. 70). The 
military macaw is a social species that congregates in small flocks and 
is often observed in mated pairs. Its clutch size is usually two to 
three eggs. They begin reproducing between 3 and 4 years of age 
(Mexican National Commission for Protected Areas [CONANP] 2006 in 
Bonilla-Ruz 2006, p. 2). Colonial nesting is believed to be due to the 
lack of suitable disbursed nest sites, which may also explain why they 
are concentrated in certain sites (Salinas-Melgoza et al. 2009, p. 
306).
    This species prefers the lower montane wet forests of the Andes. It 
inhabits remaining fragmented forested area in the Neotropics. However, 
in the northernmost part of its range, in Mexico, it is associated with 
seasonally dry, semi-deciduous tropical forest, deciduous tropical 
forest, and slopes of pine-oak forest (Bonilla-Ruz et al. 2007b, pp. 
45-47; Rivera-Ortiz et al. 2006, p. 26).
    The military macaw is a seasonal migrant, based on food and 
nutrient availability. In some areas, it has been observed at clay 
licks to obtain sodium and possibly other minerals, which is a common 
activity in some parrot species (Lee 2010, p. 58). Its diet varies 
seasonally. Some of the plant species it was observed feeding on 
include (Rivera-Ortiz et al. 2013, p. 1211; Carillo et al. 2013, p. 46; 
Huellega 2011, p. 9; Moschione 2007, in Navarro et al., 2008, p. 2; 
Contreras-Gonz[aacute]lez et al. 2006, p. 387; Renton 2004, p. 12; 
Juniper and Parr 1998, p. 422):

Brosimum alicastrum (capomo, Maya nut, ram[oacute]n),

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Bunchosia montana (no common name (ncn)),
Bursera aptera (ncn),
Bursera schlechtendalii (ncn),
Carya illinoensis (nuez de castilla),
Cedrela species (cedar fruit),
Ceiba aescutifolia (Pochote),Ceiba pentandra (ceiba),
Couepia polyandra (zapotillo),
Cyrtocarpa procera (Chupandilla),
Encyclia lancifolia (orchid, ncn),
Ficus species (fig),
Guaiacum coulteri (soap bush),
Hura crepitans (ochoo, arbol del diablo, acacu, monkey's dinner-bell, 
habillo, ceiba de leche, sand-box tree, possum wood, dynamite tree, 
ceiba blanca, assacu, posentri),
Hura polyandra (arbol del diablo, habillo, haba, jabillo, tetereta),
Ipomoea arborescens (palo santo, palo blanco, tree morning glory),
Juglans mollis (nogal),
Lonchocarpus rugosus (palo arco),
Lysiloma divaricata (ncn),
Lysiloma microphylla (palo corral),
Mangifera indica (mango),
Melia azedarach (Chinaberry tree),
Neobuxbaumia tetetzo (cardon, higos de teteche, tetetzo),
Orbignea guacoyula (palm),
Pinus ayacahuite (pinabete),
Pinus engelmannii (pino real),
Pinus durangensis (pino alaz[aacute]n),
Plumeria rubra (Frangipani),
Quercus affinis (encinos),
Quercus castanea (encinos),
Quercus crassifolia (encinos),
Spondias mombin (ciruelo),
Tecoma stans (yellow trumpetbush),
Tillandsia grandis (ncn), and
Tillandsia makoyana (ncn).

    Seeds were found to be 39 percent of this species' diet. They have 
also been observed feeding on bromeliad stems (species unknown) and 
cacti (species unknown). In the northern part of its range in Mexico, 
military macaws have been observed in desert habitat, although they 
tend to have lower reproductive success in this habitat type (Rivera-
Ortiz et al. 2008, p. 261). In desert habitat, which is suboptimal, it 
has been observed consuming some flowers (species unidentified). 
Despite the low seasonal abundance of food, deserts offer some refuge 
from poaching due to the inhospitable dry climate, which can act as a 
deterrent to poachers (Rivera-Ortiz et al. 2008, p. 261). In addition, 
macaws tend to nest at very high locations, which can make it difficult 
for poachers to reach them.

Range, Observations, and Population Estimates

    The military macaw is distributed in highly fragmented, small 
populations in Mexico and South America, with a distribution gap in 
Central America (BLI 2014a, pp. 1-2; Rivera-Ortiz 2013, p. 1,201; 
Juarez et al 2012, pp. 6-7). Its range extends from northern Mexico 
southward into Ecuador, Peru, Colombia, Venezuela, Bolivia, and the 
southern tip of Argentina (see Figure 1 for an approximation of its 
range and distribution). The species has been described as patchily 
distributed throughout the eastern foothills of the Andes Mountains 
(Snyder et al. 2000, p. 125). It occurs in altitudes up to 1,600 m 
(5,249 ft) (Strewe and Navarro 2004, p. 50; Snyder et al. 2000, pp. 
102, 124-125). Although it has a large distribution (276,000 km\2\ 
(106,564 mi\2\)), its populations are localized.
    Its population is estimated to be 6,667-13,333 mature individuals 
(BLI 2014, pp. 1-2; Rivera-Ortiz et al. 2013, p. 1,201). Most areas 
where this species occurs are now estimated to have fewer than 100 
individuals. However, in 2004, other populations in Colombia and Mexico 
were estimated to be 100-200 individuals (Fl[oacute]rez and Sierra 
2004, p. 3). This species may have occurred in Guatemala in the past, 
but it is no longer found there (Gardner 1972 in Snyder et al. 2000, p. 
125). Overall, its populations are fragmented and becoming more 
isolated (Rivera-Ortiz 2008, p. 256).
[GRAPHIC] [TIFF OMITTED] TR02OC15.009


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    The species inhabits tropical, semi-deciduous forests along the 
Pacific and Atlantic slopes through Central and South America. The best 
available information indicates there are reasonably healthy but small 
populations in El Cielo and Sierra Gorda Biosphere Reserves (Sierra 
meaning mountain range) in Mexico, Madidi and Ambor[oacute] National 
Parks, Pil[oacute]n Lajas Biosphere Reserve and Apolobamba National 
Integrated Management Area in Bolivia, and Manu Biosphere Reserve and 
Bahuaja Sonene National Park in Peru, and a small but stable remnant 
population in Tehuacan-Cuicatlan Biosphere Reserve, Oaxaca, Mexico 
(Lowry 2014, p. 3; Hosner et al. 2009, p. 222; Arizmendi 2008, p. 3; 
Rivera-Ortiz 2008, p. 256). The population from Tehuacan-Cuicatlan 
Biosphere Reserve, Oaxaca is about 100 macaws (Bonilla et al. 2007a, p. 
731).

Argentina

    Argentina is the southernmost part of this species' range, and the 
species was never thought to have been abundant there (Navarro et al. 
2008, p. 1). In fact, this species was initially thought to be 
extirpated (locally extinct) in Argentina, but surveys have found small 
populations in at least two locations in the northern province of Salta 
(Grilli et al 2013, p. 235; Juarez et al 2012, pp. 7-8). There are 
anecdotal reports of this species crossing the Ita[uacute] River 
(Navarro et al. 2008, p. 3), which borders Bolivia and Argentina. 
Between 2005 and 2007, approximately 100 individuals were observed in 
the Salta Province. These areas include: Finca Itaguazuti, and the 
Acambuco Provincial Flora and Fauna Reserve (8,266 hectares [ha] or 
20,426 acres [ac]) in the Tartagal Mountains and which borders Bolivia 
(BLI 2014; Navarro et al. 2008, pp. 1, 4; Coconier et al. 2007, p. 59). 
In 2008, flocks of between 4 and 40 individuals of this species were 
observed in three ravines in the Salta Province. These locations were 
the Agua Fresca (Cool Water) Ravine north of Campo Cauzuti, El 
Lim[oacute]n Ravine (which had the largest population), and the 
Carapar[iacute] River Ravine. These are believed to be established 
populations, rather than flocks crossing over from Bolivia (Navarro et 
al. 2008, pp. 1, 4).

Bolivia

    In Bolivia, the military macaw is regularly observed in five 
national parks: Tambopata National Reserve, Pil[oacute]n Lajas 
Biosphere Reserve, Madidi National Park, Apolobamba National Integrated 
Management Area, and Ambor[oacute] National Park (Hennessey 2011, pers. 
comm.). This species exists in the Andean foothills in Bolivia in 
forested areas extending from the northern Tambopata National Reserve 
to the southern Pil[oacute]n Lajas Reserve (Hennessey et al. 2003, pp. 
319, 329). These parks are in the general vicinity of the border of 
southern Peru and northern Bolivia (Hosner et al. 2009, p. 222; Navarro 
et al. 2008, p. 2; Hennessey et al. 2003, p. 322). They are part of the 
Greater Madidi-Tambopata Landscape (GMTL) (also known as ``Parque 
Nacional Madidi''). Within the GMTL, there are thought to be reasonably 
healthy populations of this species in the Apolobamba National 
Integrated Management Area, Ambor[oacute] and Madidi National Parks, 
and Pil[oacute]n Lajas Biosphere Reserve (Hennessey 2011 pers. comm.; 
Hosner et al. 2009, p. 225). The Greater Madidi-Tambopata Landscape is 
110,074 km\2\ (42,500 mi\2\) in size, and encompasses one of the 
largest areas of intact montane forest in the tropical Andes (WCS 2009, 
p. 2). This area is a high conservation priority due to its large 
number of endemic bird species. Pil[oacute]n Lajas consists of primary 
evergreen tropical lowland forest, foothill forest, and lower montane 
forest. Pil[oacute]n Lajas was recognized as a Biosphere Reserve and 
Indigenous Territory by the Bolivian Government in 1992; however, it 
did not have any actual protections in place until 1994 (Hennessey et 
al. 2003, p. 319).
    In 2008, this species was observed at Serran[iacute]a Sadiri in 
Madidi National Park, La Paz Department, Bolivia (Hosner et al. 2009, 
p. 225). Serran[iacute]a Sadiri is found just inside Madidi National 
Park. Here, flocks of between 2 and 36 individuals have been observed 
(Hosner et al. 2009, p. 228). The Pil[oacute]n Lajas Biosphere Reserve 
is primarily in La Paz Department, but slightly overlaps into the Beni 
Department. Here, this species is described as uncommon (Hennessey 
2003, p. 329). It was observed in Parapetiguasu-Taremakua, and 
Parapetiguas-Uruwigua in Santa Cruz, Cordillera Province, and at 
Altamachi and Madidi in Cochabamba, Ayopaya Province (MacLeod 2009, pp. 
42-43). In summary, within Bolivia, there are many small populations of 
this species in areas that provide suitable habitat for this species 
(primarily large forest patches under some form of protection).

Colombia

    In the late 1990s, there were approximately five disjunct 
populations in the central Andes Mountains (Snyder et al. 2000, p. 
125). In Colombia, groups of 50 individuals have been observed, and in 
one case, a population was estimated to have 156 individuals 
(Fl[oacute]rez and Sierra 2004, pp. 2-3). In most cases, these 
individuals reside on cliff formations that are favorable for nesting 
(where they are less accessible to poachers), and where deforestation 
is having less of an impact (Fl[oacute]rez and Sierra 2004, pp. 2-3; 
Rodriguez and Hern[aacute]ndez-Camacho 2002, p. 203). In Colombia, this 
species inhabits a wide range of altitudes and areas with various 
degrees of alteration (Fl[oacute]rez and Sierra 2004, pp. 1-3; Juniper 
and Parr 1998). In Colombia, this species has been observed between 
altitudes of 700 and 1,600 m (2,297 to 5,249 ft) (Fl[oacute]rez and 
Sierra 2004, pp. 1-3; Salaman et al. 2002, pp. 167, 187). Populations 
have been observed in Guajira peninsula, Las Orquideas, Tayrona 
National Park, Serran[iacute]a de Perij[aacute], Serran[iacute]a de San 
Lucas, San Salvador Valley, Sierra Nevada De Santa Marta, La Guajira 
Department, and Cueva de los Guacharos National Park (Strewe and 
Navarro 2003, p. 3). In 1998, this species was observed in flocks of up 
to 12 individuals at Villa Iguana and Alto Cagadero in Serran[iacute]a 
de los Churumbelos (Salaman et al. 2007, pp. 33, 38, 47, 89). It has 
been observed in palm stands in the San Salvador valley during the 
breeding season (December-July) (Strewe and Navarro 2003, p. 33).
    There are two small, stable populations of military macaws at 
Sierra Nevada de Santa Marta and Churumbelos, Cauca, with approximately 
50 mature birds at each site (Fundaci[oacute]n ProAves 2011, p. 28). In 
2004, Fl[oacute]rez and Sierra estimated that the population in the 
cliffs of the Cauca River was 156 individuals and contained 54 breeding 
pairs and 26 nests (2004, p. 3). However, this population is subjected 
to impacts from poaching and deforestation (Fl[oacute]rez and Sierra, 
2004, pp. 3-4), so the population now may be smaller. These researchers 
also noted that many chicks fall from the cliff nests and die. As of 
2011, there were no recent records in northern Antioquia (Paramillo), 
Serran[iacute]a de San Lucas, or Perij[aacute] ranges (Fundaci[oacute]n 
ProAves 2011, pp. 28-29).
    In the Fr[iacute]o Valley of Colombia, this species is reported to 
be present only during the breeding season (Strewe and Navarro 2004, p. 
50). Several nests were found here in forest fragments. A population at 
El Congo Reserve was intensively studied in 2001. One nest was located 
12 m (39 ft) above ground in a Ceiba tree, within open primary forest 
on a steep slope at 900 m (2,953 ft). A breeding population of 12 
pairs, with groups of up to 28 was observed in December 2000. However, 
here it is still threatened in the valley by habitat loss and domestic 
trade (two cases noted in 2001) (Strewe and Navarro

[[Page 59981]]

2004, p. 50), and the population may now be decimated.

Ecuador

    In Ecuador, this species is considered to be very rare (Arcos-
Torres and Solano-Ugalde 2008, p. 71). This species has been observed 
in the areas of Sumaco and Zamora-Chinchipe in Ecuador (Snyder et al. 
2000, p. 125) and at Kichwa River Reserve (Reserva Kichwa R[iacute]o), 
within the Gran Sumaco Guacamayos Biosphere Reserve (Arcos-Torres and 
Solano-Ugalde 2008, p. 72). Most records of military macaw in Ecuador 
during the 1980s and 1990s found groups of up to 20 individuals 
(Ridgely and Greenfield 2001); however, lately most records have not 
exceeded 8 individuals (Arcos-Torres and Solano-Ugalde 2008, p. 71) 
except for a breeding colony of 16 individuals that was observed in the 
Reserva Kichwa R[iacute]o (Arcos-Torres and Solano-Ugalde 2008, pp. 70-
72). Prior to 1980, it was observed in the upper Upano River Valley 
(Ridgely 1980 p. 244). In 2006, 200 ha (494 ac) were turned into the 
Narupa Reserve, where this species was observed in approximately 2010 
(Fundaci[oacute]n ProAves et al. 2010, p. 42). Additionally, in 2010, a 
pair of military macaws was observed in northern Ecuador in the Sumaco 
region (Olah and Barnes 2010, p. 19).

Mexico

    There are several small populations of military macaws in Mexico, 
each consisting of between approximately 20 and 90 individuals 
(Jimenez-Arcos et al. 2012, p. 864; Rivera-Ortiz et al. 2008, p. 256), 
although there has been an anecdotal report of a population estimated 
to be 130 individuals (Bonilla 2012, p. 6). This species follows 
seasonal food sources, so flocks move to other areas seasonally. In 
Mexico, there are reasonably healthy but small populations in the 
following areas:

 Alamos Rio Cuchujaqui (Sonora),
 Puerto Vallarta (Jalisco),
 Tehuacan-Cuicatlan Biosphere Reserve (at the border of Puebla 
and Oaxaca States) Mineral de Nuestra Se[ntilde]ora Reserve (Sinaloa),
 El Cielo Biosphere Reserve (Tamaulipas),
 Sierra Gorda Biosphere Reserve (Quer[eacute]taro),
 Sierra Manantl[aacute]n Biosphere Reserve (Jalisco),
 Vicinity of Copalillo (Guerrero) (Jimenez-Arcos et al. 2012, 
p. 865).
[GRAPHIC] [TIFF OMITTED] TR02OC15.010

    In Mexico, there may also be isolated populations of military 
macaws in other States. Figure 2 shows the approximate present day and 
historical distribution of the military macaw in Mexico as of 2008 
(Arizmendi 2008, p. 4). Other States where it may exist include Colima, 
Durango, Michoac[aacute]n, Morelos, Nayarit (in the Valley of Flags or 
``Valle de Banderas''), Nuevo Le[oacute]n, San Luis Potos[iacute], and 
Zacatecas. Areas where it has been recently documented are described 
below.

Chihuahua

    Researchers believe there is a remaining population in the Sierra 
Madre Occidental Mountains (north-central Mexico) in Otachique (Cruz-
Nieto et al. 2006, p. 14). In 2005, 25 nests were observed (Cruz-Nieto 
et al. 2006, p. 14). This canyon is approximately 700 m (0.5 miles) 
wide by 14 km (8.6 miles) in length and consists of mature pines, firs, 
and oaks. Some gallery temperate forest remains in this area.

[[Page 59982]]

Guerrero

    A colony of approximately 20 military macaws was studied between 
2006 and 2010 in the vicinity of Copalillo, Guerrero (Jim[eacute]nez-
Arcos et al. 2012, pp. 864-865). The vegetation is tropical deciduous 
forest; and a canyon is present.

Jalisco

    This species is found sporadically in small groups of a few to 
approximately 100 macaws in the western foothills of Sierra del Cuale 
and Sierra Cacoma in Jalisco on the western coast of Mexico (Renton 
2004, pp. 13-14). Other groups of macaws in the region are in Cabo 
Corrientes in the Horcones river basin (approximately 100 macaws). 
There are other small populations in the vicinity of Puerto Vallarta 
(Carrillo et al. 2013, pp. 45, 47). This species was observed in 2004 
near a freshwater lake, Caj[oacute]n de Pe[ntilde]a (26 by 9 km (16 by 
5.6 mi) in size), which was constructed in 1976. It is found in the 
Chamela-Cuixmala Biosphere Reserve (132,000 ha or 32,617 ac), which is 
managed by Mexico's Instituto de Ecologia of the National Autonomous 
University of Mexico (UNAM) and nongovernmental organizations (NGOs). 
Patches of semi-deciduous forest in this area form corridors between 
existing protected areas, such as the Chamela-Cuixmala and the Sierra 
Manatl[aacute]n Biosphere Reserves (Renton 2004, p. 14). These patches 
likely have served as critical ecological links for this species.

Oaxaca

    This species has recently been the focus of research in Sabino 
Canyon, Oaxaca. Sabino Canyon is in the Tehuacan-Cuicatlan Biosphere 
Reserve (Reserva de la Biosfera Tehuacan Cuicatlan), created in 1998, 
in central Mexico. The reserve spans 490,187 ha (1,211,278 ac) and is 
located within the Mixteca Oaxaque[ntilde]a Province between the cities 
of Puebla and Or[iacute]zaba. It is approximately 150 km (93 mi) 
southeast of Mexico City (http://www.parkswatch.org, accessed July 11, 
2011) and approximately 2 hours from Tehuacan, Oaxaca, Mexico. Large 
mountain ranges delineate the boundaries of the reserve, and six rivers 
are within the protected area's boundaries.
    In 2001, this species was observed in two canyons within this 
reserve. In both ravines, 20 pairs were observed nesting (Salazar-
Torres 2001, p. 18). Here, this species nests in the canyon cliff walls 
in crevices that can be as high as 250 m (820 ft). Between 2002 and 
2004, approximately 100 individual military macaws were observed 
(Bonilla-Ruz et al. 2007a, p. 729). During 2007-2008, at least 67 birds 
were observed during the month of August (Rivera-Ortiz et al. 2008, p. 
256; Rivera-Ortiz et al. 2006, p. 26). The known nesting site locations 
within the reserve increased from five to nine during the study period 
(Rivera-Ortiz et al. 2006, p. 28). Currently in the Sabino Canyon, the 
population of military macaws is thought to be between 90 and 100 
individuals (Arizmendi 2008, p. 15).

Sinaloa

    This species exists in Mineral de Nuestra Se[ntilde]ora de la 
Candelaria Ecological Preserve, 12 km (7.4 mi) southeast of the town of 
Cosala in Sinaloa, Mexico (Rubio et al. 2007, p. 52; Bonilla-Ruz et al. 
2007b, p. 45). The preserve is 1,256 ha (3,104 ac) and consists of dry 
tropical forest. In 2002, this area was designated as a protected area 
by the State of Sinaloa Decree.

Sonora

    Between 2008 and 2009, it was observed at the Northern Jaguar 
Reserve in east-central Sonora, and was described as a rare summer 
resident there (Flesch 2009, pp. 5, 12). In this area, this species was 
recently observed in small flocks in cliff areas (Flesch 2008, pp. 35-
36). In 2005, it was observed in the R[iacute]o Aros canyon and upper 
R[iacute]o Yaqui valley in an area known as the Yaqui Basin (O'Brien et 
al. 2006, pp. 4, 27-28). Flesch suggests that the species is likely to 
occur only in cliffs near stands of tropical vegetation (full citation 
2008, p. 27).

Tamaulipas

    Historically, in Mexico's eastern State of Tamaulipas, flocks of 
approximately 60 individuals were noted almost daily in the area of 
G[oacute]mez Far[iacute]as, Mexico (Sutton and Pettingill 1942, p. 14). 
The G[oacute]mez Far[iacute]as region is on the eastern slope of the 
Sierra Madre Oriental mountain range, known locally as the ``Sierra de 
Guatemala.'' This area is in the general vicinity of the state-
protected El Cielo Biosphere Reserve, where this species is still known 
to occur (Arvin 2001, p. 8). The University of Texas at Brownsville 
maintains a research station, Rancho del Cielo, within the 145,687-
hectare (360,000-acre) reserve. The research station supports locally 
driven scientific research and community development (University of 
Texas at Brownsville, unpaginated). Activities conducted by the 
research station have positive impacts on this species by attracting 
researchers and the birding community, preserving and protecting 
habitat, and creating awareness in the area.

Peru

    There are populations in Manu Biosphere Reserve, Tambopata National 
Reserve, and Bahuaja Sonene National Park in Peru. The two latter parks 
border one another in the southern Peruvian Amazon region (ParksWatch 
2002, p. 1). This species has been observed around the Pongo de 
Mainique of the Urubamba River and on the upper Tambopata River (Snyder 
et al. 2000, p. 125). According to a 2010 paper, it was observed in the 
Madre de Dios department in the southeastern Peruvian Amazon (Lee 2010, 
p. 14). Flocks of 40 to 50 individuals have been observed in Atalya at 
Madre de Dios (Snyder et al. 2000, p. 125). The species has been 
observed seasonally in small numbers in the area of the Hu[aacute]llaga 
River Canyon (JGP Consultants 2011 pp. 1, 5, 8).

Venezuela

    Within Venezuela, it has been documented primarily within protected 
areas. In this country, little information about the species exists 
(Rodriguez et al. 2004, pp. 375-376). Here it persists in the Andes in 
the Central Coastal Cordillera and Sierra de Perij[aacute] (Rodriguez 
et al. 2004, pp. 375, 378, 379). It has been found on the north slopes 
of El [Aacute]vila, Guatopo, Henri Pittier National Park, the State of 
Cojedes, Cerro La Misi[oacute]n, and Sierra de Perij[aacute] National 
Park (Desenne and Strahl 1994 and Fernandez-Badillo et al. 1994 in 
Snyder et al. 2000, p. 125). A new population of this species was 
recorded at two localities at the Catatumbo-Bar[iacute] National Park 
along the Colombian-Venezuelan border (Avenda[ntilde]o 2011, p. 2). 
Moist forests exist as four distinct enclaves within the Catatumbo 
Valley, in both northwestern Venezuela and northeastern Colombia. This 
extends the species' previously known range from the east slope of the 
Serran[iacute]a de Perij[aacute] southwards (Avenda[ntilde]o 2011, p. 
2).

Summary of Range

    According to several surveys, the military macaw exists in small 
populations ranging from a few pairs to approximately 100 individuals. 
It is found in protected areas in Mexico, Colombia, Bolivia, and to a 
lesser extent, in Ecuador, Peru, Venezuela, and Argentina (see Figure 
1), and is unlikely to exist in small populations outside of protected 
areas where large expanses of suitable habitat still remain (Bonilla 
2012, p. 9). The population in the Pil[oacute]n Lajas Biosphere 
Reserve, Bolivia, may

[[Page 59983]]

serve as a link to other populations of this species to the northwest 
and to the south (Hennessey et al. 2003, pp. 330-331). Records indicate 
that this species occurs primarily in protected areas (Flesch 2009; 
MacLeod 2009; Flesch 2008; Fl[oacute]rez and Sierra 2004; Rodriguez 
2004; Renton 2004; Hennessey et al. 2003), such as protected parks 
where there are large remaining areas of suitable habitat for nesting, 
feeding, and breeding (see Figure 1).

Summary of Population Estimate

    There are various but imprecise population estimates for the 
military macaw. One report estimates the population to be fewer than 
10,000 individuals (Arizmendi 2008, p. 3). BLI reports that the 
population is estimated to be between 10,000 and 19,999 mature 
individuals with a decreasing trend (BLI 2014, p. 2). We believe that 
the population is significantly fewer than 10,000 based on recent 
documented observations of this species, most of which are described in 
this status review. Researchers in Colombia agree with our conclusion 
(Botero-Delgadillo and P[aacute]ez 2011, p. 13). Published literature 
(referenced in this document) has documented small flocks ranging from 
approximately 16 to 156 individuals distributed in disjunct locations 
in Mexico, Argentina, Ecuador, Venezuela, Peru, Colombia, and Bolivia. 
In situations where the species is rare or has small populations, the 
number of observations made per survey may be very small and the number 
of sites limited, and, therefore, estimates may not be accurate 
(Pollack 2006, p. 891).
    The current total population number is unclear; however, based on 
these recent records, we believe that the population is between a few 
thousand and 10,000 remaining individuals (BLI 2014, p. 1; Bonilla 
2012, p. 9).

Conservation Status

International Union for Conservation of Nature (IUCN)

    There are various protections in place for this species at the 
international, national, and local levels. At the international level, 
this species is listed as vulnerable by the IUCN (2011). However, this 
status under IUCN conveys no actual protections to the species.

CITES

    The military macaw is protected by the Convention on International 
Trade in Endangered Species of Wild Fauna and Flora (CITES), which is 
one of the most important means of controlling international trade in 
animal and plant species affected by trade. CITES is an international 
agreement through which member countries, called Parties, work together 
to ensure that international trade in CITES-listed animals and plants 
is not detrimental to the survival of wild populations by regulating 
their import, export, and reexport. All of the range countries for this 
species are Parties to CITES (http://www.cites.org/eng/disc/parties/alphabet.php, accessed May 7, 2014). Most psittacines (parrots), 
including the military macaw, were included in CITES Appendix II in 
1981. An Appendix-II listing includes species not necessarily 
threatened with extinction, but in which trade must be controlled in 
order to avoid utilization incompatible with their survival. The 
military macaw was transferred to Appendix I of CITES in 1987, because 
populations were declining rapidly due to uncontrolled trapping for the 
international pet bird trade. An Appendix-I listing includes species 
threatened with extinction whose trade is permitted only under 
exceptional circumstances, which generally precludes commercial trade.

WBCA

    The import of the military macaw into the United States is also 
regulated by the Wild Bird Conservation Act (WBCA) (16 U.S.C. 4901 et 
seq.), which was enacted on October 23, 1992, in an effort to ensure 
that exotic bird species are not adversely affected by U.S. trade. The 
purpose of the WBCA is to promote the conservation of CITES-listed 
exotic birds by ensuring that all imports into the United States are 
(1) sustainable and (2) not detrimental to the species. Permits may be 
issued to allow imports of listed birds for scientific research, 
zoological breeding or display, or as personal pets when certain 
criteria are met. The Service may approve cooperative breeding programs 
and subsequently issue import permits under such programs. Wild-caught 
birds may be imported into the United States if the Service approves a 
management plan for their sustainable use. At this time, the military 
macaw is not part of a Service-approved cooperative breeding program 
and does not have an approved management plan for wild-caught birds.

Argentina

    This species is considered to be a critically endangered species by 
the Government of Argentina (Navarro et al. 2008, p. 1). It is 
protected through national legislation (Law 22.421 and Decree 691/81), 
administered by the Direcci[oacute]n Nacional de Fauna y Flora 
Silvestres. Law 22.421 addresses the Conservation of Fauna, enacted in 
1981. Decree 691/81 addresses the protection and conservation of wild 
fauna and is implemented through law 22.421.

Bolivia

    In Bolivia, this species is listed as vulnerable. The 1975 Law on 
Wildlife, National Parks, Hunting and Fishing (Decree Law No. 12,301 
1975, pp. 1-34) has the fundamental objective of protecting the 
country's natural resources. This law governs the protection, 
management, utilization, transportation, and selling of wildlife and 
their products. It also governs the protection of endangered species, 
habitat conservation of fauna and flora, and the declaration of 
national parks, biological reserves, refuges, and wildlife sanctuaries.

Colombia

    Colombia categorizes this species as ``vulnerable'' (Salaman et al. 
2009, p. 21). A vulnerable species is considered to be one that is not 
in imminent danger of extinction in the near future, but it could be if 
natural population trends continue downward and deterioration of its 
range continues (EcoLex 2002, p. 10).

Ecuador

    In Ecuador, this species is considered endangered, ``en peligro de 
extinci[oacute]n''. Here, this species is considered to be very rare 
(Arcos-Torres and Solano-Ugalde 2008, p. 69).

Mexico

    In Mexico, the military macaw is protected as endangered under 
Mexico's Wildlife Protection Act (Benetiz-Diaz 2012, p. 2) and has been 
highlighted as a priority species for conservation in the Mexican 
Parrot Conservation Plan (Rivera-Ortiz et al. 2008, p. 256; Renton 
2004, p. 12). Its official list of endangered and threatened bird 
species is termed the Norma Oficial Mexicana 059 (NOM-059, 2010) 
(Benetiz-Diaz 2012, p. 2).

Peru

    In Peru, this species is listed as vulnerable and its protections 
fall under the jurisdiction of the National Institute of Natural 
Resources (Instituto Nacional de Recursos Naturales, INRENA). Peru's 
Supreme Decree No. 034-2004-AG (2004, p. 276,855) prohibits hunting, 
take, transport, and trade of protected species, except as permitted by 
regulation.

Venezuela

    In Venezuela, this species is listed as endangered (Rodriguez et 
al. 2004, p. 376).

[[Page 59984]]

NGO Involvement

    In the 1980s, conservationists realized the value of identifying 
areas or habitat in terms of numbers of endemic bird species. BirdLife 
International, in partnership with countries, other nongovernmental 
organizations (NGOs), and various other partners, developed the 
Important Bird Area (IBA) program, which is a worldwide initiative to 
identify and protect critical areas for bird conservation. IBAs are 
areas that regularly contain significant numbers of one or more 
globally threatened species or other species of global conservation 
concern. One of the criteria in identifying important regions for bird 
conservation is the distribution of restricted-range and globally 
threatened species such as the military macaw. As of 2007, more than 
8,500 IBAs had been identified worldwide (Garc[iacute]a-Moreno et al. 
2007, p. 324). The military macaw is included in 37 of those IBAs (BLI 
2011b, pers. comm.). Note that this does not mean this species always 
occupies those areas; rather, the species has been identified in those 
areas.
    A number of locally based and international conservation 
organizations have developed programs in connection with protected 
areas within this species' range, such as ecotourism, to observe clay 
lick areas (Lee 2010, pp. 167-168). The Wildlife Conservation Society 
(WCS) is implementing a range of projects aimed at strengthening the 
management of Greater Madidi-Tambopata Landscape in Bolivia. Its 
program is based on three main categories: (1) Park management, (2) 
natural resources management, and (3) scientific research (Parks Watch 
2005, pp. 2-3). The Greater Madidi-Tambopata Landscape, where the WCS 
is monitoring populations of the military macaw (WCS 2009, pp. 2, 8), 
encompasses one of the largest swaths of intact montane forest in the 
Tropical Andes in northern Bolivia and southern Peru. The GMTL is 
110,074 km\2\ (42,500 mi\2\) and includes five protected areas.
    A Colombian-based NGO, Fundaci[oacute]n ProAves, is also working to 
protect this species and its habitats. Fundaci[oacute]n ProAves 
developed a conservation plan for 2010 to 2020 for several parrot 
species, including the military macaw (Botero-Delgadillo and 
P[aacute]ez 2011, p. 7). However, it is unclear if or when it will be 
adopted by the Government of Colombia.
    In Mexico, several NGOs are participating in the conservation and 
management of this species. In 1989, a strong citizen movement began to 
conserve the 383,567-ha (947,815-ac) Sierra Gorda Biosphere Reserve by 
establishing the local group, Grupo Ecol[oacute]gico Sierra Gorda. In 
collaboration with the local community, this group has taken action to 
protect bird communities as well as other groups of wildlife in this 
area. Strategies include environmental education, establishment of 
private reserves, and payment for environmental services in a 25,000-ha 
(61,776-ac) area of this reserve (Pedraza-Ruiz, 2008 p. 1). The 
Chamela-Cuixmala Biosphere Reserve is managed by Mexico's Instituto de 
Ecologia of the National Autonomous University of Mexico (UNAM) and 
local NGOs. Other NGOs are working with communities to obtain macaw 
feathers from aviaries so that indigenous people will not hunt the 
macaws for their feathers (Renton 2004, p. 14). In the Sinaloa area, 
the Universidad Aut[oacute]noma de Sinaloa has been active in 
conservation of this species since 1998 (Rubio et al. 2007, p. 52). 
This university conducts research outreach activities to foster 
knowledge, and conservation of this species at the Mineral de Nuestra 
Se[ntilde]ora de la Candelaria Ecological Preserve.

Evaluation of Threat Factors

Introduction

    Section 4 of the ESA (16 U.S.C. 1533) and implementing regulations 
(50 CFR 424) set forth procedures for adding species to, removing 
species from, or reclassifying species on the Federal Lists of 
Endangered and Threatened Wildlife and Plants. Under section 4(a)(1) of 
the ESA, a species may be determined to be endangered or threatened 
based on any of the following five factors:

A. The present or threatened destruction, modification, or curtailment 
of its habitat or range;
B. Overutilization for commercial, recreational, scientific, or 
educational purposes;
C. Disease or predation;
D. The inadequacy of existing regulatory mechanisms; and
E. Other natural or manmade factors affecting its continued existence.

    Throughout the range of this species, the factors impacting this 
species are generally very similar. The primary factors affecting the 
military macaw are habitat loss and degradation, and poaching (Carrillo 
et al. 2013, p. 46; Gasta[ntilde]aga et al. 2011, entire; Strewe and 
Navarro 2004, p. 50). Habitat loss is primarily due to conversion of 
the species' habitat (generally forests) to agriculture and other forms 
that are not optimal for the military macaw (Donald et al. 2010, p. 26; 
Fl[oacute]rez and Sierra 2004, p. 3). Conversion of habitat to soy 
plantations is now considered to be one of the principal causes of 
Amazon deforestation (Bonilha 2008, p. 17). Because this species has a 
small and fragmented population, poaching, while apparently uncommon, 
remains a concern (Botero-Delgadillo and P[aacute]ez 2011, p. 13).
    We focus primarily on where this species has been documented, 
particularly in parks and other areas with protected status and the 
peripheral zones. In some cases, we will evaluate the factor by 
country. In other cases, we may evaluate the factor by a broader region 
if we do not have adequate information specific to a particular country 
about this species. This is because often the threats are the same or 
very similar throughout the species' range.

A. The Present or Threatened Destruction, Modification, or Curtailment 
of Its Habitat or Range

Habitat

    The military macaw has a large but fragmented distribution (276,000 
km\2\ (106,564 mi\2\)), and not all locations where the military macaw 
exists are known (BLI 2014, p. 1). Habitat destruction and modification 
is one of the main threats to the military macaw; significant amounts 
of this species' habitat have been converted such that its habitat is 
no longer suitable and no longer provides adequate shelter (nesting 
sites) and food sources, and these causes of habitat loss are likely to 
continue (Marin-Togo et al. 2012, p. 462). Between 2000 and 2005, of 
all the continents, South America had the largest net loss of forested 
area, experiencing a loss of 4.3 million ha (10.6 million ac) per year 
(FAO 2006 in Mosandl et al. 2008, p. 38). In some countries, extractive 
activities for nontimber forest products occur, such as the removal of 
palm trees (Arecaceae family) to obtain hearts of palm (ParksWatch 
2011; http://www.tropicalforestresearch.org).
    Currently, the military macaw exists in many parks and other areas 
that have protected status (Mar[iacute]n-Togo et al. 2012, p. 465; 
Coconier et al. 2009, p. 63; Arizmendi 2008, p. 4; Rodriguez et al. 
2004, p. 78; Renton 2004, p. 12). Studies have found that, compared 
with the surrounding areas, conditions inside parks were significantly 
better than their surrounding counterparts (Bruner et al. 2001, p. 
125). One study found that, in 40 percent of tropical parks, land that 
had formerly been under cultivation and that was incorporated into park 
boundaries had recovered. This subsequently led to an increase in 
vegetative cover. The study found that

[[Page 59985]]

83 percent of parks were successful at mitigating encroachment (Bruner 
et al. 2001, p. 125). This was confirmed in a study published in 2007 
that found that forests in conservation units were four times better at 
protecting against deforestation than unprotected areas (Oliveira et 
al. 2007, p. 1,235). However, this species still faces habitat loss 
(Benetiz 2012, p. 4).
    We are limiting our analysis to areas where there is information 
available about this species. For instance, there is very little 
information available about this species in Argentina and Venezuela 
(Coconier et al. 2009, p. 63; Navarro et al. 2008, p. 1; Coconier et 
al. 2007, p. 52; Rodriguez et al. 2004, pp. 378-379). However, in both 
of these countries, the species faces similar threats (such as the lack 
of suitable habitat) as in other countries (Rodriguez et al. 2004, p. 
373). The largest populations of this species, discussed in detail in 
the Range, Observations, and Population Estimates section, appear to be 
in Mexico and Bolivia. Even in these countries, its populations are 
small and fragmented. In other countries within its range such as 
Colombia, Peru, and Ecuador, it exists in smaller populations, and 
Argentina (Nores and Yzurieta 1994, pp. 315-316) and Venezuela have 
even smaller and possibly negligible populations. Additionally, the 
military macaw may have occurred in Guatemala in the past, but it is no 
longer found there (Gardner 1972 in Snyder et al. 2000, p. 125).

Argentina

    In Argentina, habitat destruction, particularly deforestation for 
agricultural expansion for soy plantations, and timber extraction had 
significantly increased as of 2009 (Devenish 2009, p. 60; Chebez et al. 
in litt. in Navarro et al. 2008, pp. 7, 9; DiPaola et al. 2008, pp. 1, 
8). The species was thought to no longer exist in Argentina, which is 
the southernmost part of its range, but recent surveys found small 
populations of this species in at least two locations in the Salta 
Province (Navarro et al. 2008, p. 1). The primary threat to forested 
areas in Argentina is the expansion of agriculture, particularly soy, 
into remaining habitat such as the Chaco plains in the Andes mountain 
range (Centro de Acci[oacute]n Popular Olga M[aacute]rqu[eacute]z de 
Aredez (CAPOMA) 2009, p. 6). The practice of drying swamps through 
channeling is common in northern Argentina, particularly for producing 
soybeans, which is experiencing increasing demand in the global market. 
The current rate of deforestation stands at 25,000 ha (61,776 ac) per 
year resulting from land converted to agricultural use (Devenish 2009, 
p. 60). The area converted to soy production increased from as little 
as 3 percent in the 1970s to 40 percent of the total crop area in 2003, 
covering 14 million ha (34.6 million ac) (Devenish 2009, p. 60). 
Conversion of lands to soy production is favored by the current 
political and economic climate, both at the global and national levels 
(Devenish 2009, p. 60). With regard to other types of land use, the 
area used for cattle ranching has decreased, but exotic tree 
plantations have doubled (Devenish 2009, p. 60).
    In addition, pipeline routes and associated roads are being 
established in this area in connection with oil, gas, and mineral 
exploration (Navarro et al. 2008, pp. 7, 9). Road building operations 
greatly facilitate access to large, previously inaccessible forested 
areas (Fimbel et al. 2001, pp. 511-512). The area occupied by permanent 
facilities including pipelines and refineries is relatively small, but 
oil development areas cover large tracts of land. Oil development can 
have significant negative impacts on nearby habitat through 
construction of roads and other buildings, discharge of contaminants, 
and oil spills and leaks (Gay et al undated, pp. 2-6).
    Although some of this species' habitat is protected, its habitat 
continues to shrink in Argentina. In the area of Acambuco, where the 
military macaw has been observed, the designation of Acambuco Reserve 
as a provincial reserve provides some protective measures. The purposes 
of this reserve, in part, are to preserve its genetic resources, to 
preserve the environment surrounding catch basins of its rivers, and to 
guarantee the maintenance of the biodiversity living in the reserve. 
However, in the Salta Province, this species is primarily found in 
areas that are unprotected, with the exception of the Acambuco Reserve 
(Navarro et al. 2008, pp. 1, 7, 9). In summary, significant amounts of 
this species' habitat have been converted such that its habitat is no 
longer suitable, and these causes of habitat loss are likely to 
continue.

Bolivia

    Madidi National Park experiences threats that are representative of 
threats to this species' habitat in Bolivia. The park is one of the key 
areas where this species likely has a viable population in Bolivia. 
Thus, we focused our analysis on this park. The National Service of 
Protected Areas (SERNAP) has authority over Bolivia's parks and 
protected lands. Approximately 53 percent (57.2 million ha; 141.3 
million ac) of Bolivia's total area is forested (FAO 2010, p. 228). Of 
this area, 38.9 million ha (96.1 million ac) are within the Bolivian 
Amazon and constitute 5 percent of the total Amazon forest (Locklin and 
Haack 2003, p. 774). As of 2005, Bolivia had 12 national parks, 
including 6 with integrated management natural areas, 1 with indigenous 
territory (or communal lands), and 4 national reserves; 2 biosphere 
reserves; and 3 integrated management natural areas, totaling 
16,834,380 ha (41,598,659 ac) (ParksWatch 2005, p. 2). A discussion of 
typical threats in Bolivia's parks follows. The region suffers from 
chronic and intense poverty levels, which affect more than 90 percent 
of the population (Instituto Nacional de Estad[iacute]stica de Bolivia 
(INE) 2005). The result is intense conflict between development and 
conservation. In Madidi National Park, the three greatest threats to 
the nature preserve are the construction of a highway within the park, 
drilling for oil, and a planned hydroelectric dam. Other activities 
that are impacting or are likely to impact this park are illegal 
logging, gold mining, and uncontrolled tourism (ParksWatch 2011b, pp. 
1-15; Chavez 2010, pp. 1-2).
Deforestation and Logging
    The forests of Bolivia have mainly been subjected to selective 
logging (Salo and Toivonen 2009, p. 610; Fredericksen 2003, p. 10), 
which has been done at very low levels and with low human pressures 
(Pacheco 2006, p. 206), allowing them so far to remain largely intact. 
In the five national parks where the military macaw is regularly 
observed, there are some protections in place for the species' habitat 
(Hennessey 2011, pers. comm.). However, logging still occurs within the 
range of this species (ParksWatch 2011b, p. 1). Large tracts of primary 
forest remain in Bolivia, but it is likely that some of these will be 
subjected to logging (Fredericksen 2003, p. 13) due to slash-and-burn 
activities by indigenous communities, and because forest products are 
one of Bolivia's primary exports (Byers and Israel 2008, p. vi). The 
use of slash-and-burn practices on steep and erodible slopes has 
considerably affected the area's hydrological regime, particularly near 
the city of Santa Cruz. In many areas of human settlement, soil erosion 
is compounded by logging, nutrient depletion, and weed invasion.
    As of 2006, 89 timber companies held the rights to 5.8 million ha 
(14.3 million ac) of logging concessions (Pacheco 2006, p. 208). The 
Bolivian Forestry Law of 1996 (Forestry Law 1700)

[[Page 59986]]

requires the preparation and approval of management plans and adherence 
to best management practices (BMPs) (Fredericksen 2003, p. 10). For 
instance, harvesters must pre-map harvestable trees (which have minimum 
diameter limits), protect seed trees, and set aside areas that are 
designated as protected or not harvestable. Management issues still 
need to be addressed, including sufficient regeneration time for 
commercial species (Fredericksen 2003, p. 10). However, Bolivia 
continues to attempt to balance the use of its natural resources with 
competing priorities. For example, the Pil[oacute]n Lajas Management 
Plan divided the reserve into specific zones to combine indigenous 
community rights with conservation initiatives (Hennessey et al. 2003, 
p. 320). Despite national laws and regulations, activities such as 
illegal timber extraction continue to spread unabated (World Bank 2006, 
p. 8; U.S. Forest Service 2007, p. 2; Pacheco 2006, p. 208).
Roads
    There are increasing demands for road infrastructure within Bolivia 
for many reasons. It is one of the poorest countries in South America 
(MacLeod 2009, p. 6; INE 2005), and the government would like to 
improve its economy (ParksWatch 2011b, p. 13). The construction of the 
Apolo-Ixiamas Road is one way of facilitating access to its natural 
resources. A road has been proposed that would bisect the Madidi 
National Park and Natural Integrated Management Area, opening vast, 
currently inaccessible tropical forest areas to colonization and 
resource extraction (ParksWatch 2011b, pp. 1-2). This can promote 
illegal logging, and facilitate access to previously inaccessible 
forested areas (Fimbel et al. 2001, pp. 511-512). The construction of 
roads through this park has been a source of controversy for several 
years http://conservation-strategy.org/sites/default/files/field-file/6_Madidi_Road_Complete_Document.PDF, accessed May 6, 2014). The current 
status of the road and whether it will be constructed around the park 
or through the park remains unclear. However, regional development 
plans are often implemented without consideration of impacts on natural 
resources (WCS 2009, p. 4). Plans to connect Bolivia and Peru to 
Brazil's expanding markets and expand the energy industry (oil and gas) 
will affect fragile areas of high biodiversity (WCS 2009, p. 4). Roads 
constructed in the past have also been problematic. In the late 1990s, 
roads through Serran[iacute]a Sadiri spurred an increase in 
unsustainable logging of the area's mahogany trees, which were the most 
valuable tree at the time (World Land Trust 2010, p. 1).
Hydroelectric Power
    Possibly one of the greatest threats in the Madidi National Park is 
the proposed Bala Hydroelectric Dam Project at the Beni River in the 
Bala Gorge, where the Beni River goes through the Bala Mountain Range. 
The Bala Hydroelectric Dam, as proposed, could flood much of Madidi 
National Park and the adjacent biosphere reserve and indigenous 
territory Pil[oacute]n Lajas, which is an area of about 2,000 km\2\ 
(4,942 mi\2\) (Chavez 2010, pp. 1-2; Bolivia Supreme Decree 24191). 
Construction of dams can have severe impacts on ecosystems (McCartney 
et al. 2001, p. v). For example, a dam blocks the flow of sediment 
downstream. During construction of dams, disturbance to soils at the 
construction site is one of the largest concerns. This leads to 
downstream erosion and increased sediment buildup in a reservoir. 
Although the current status of this dam is unclear, it is clear that 
the Government of Bolivia is intent on becoming more self-reliant, in 
part through creating its own sources of energy through hydroelectric 
dams.
Other Pressures
    In Madidi National Park, there is limited legal hunting, but in the 
areas surveyed, this species was described as common and not exploited 
(Hosner et al. 2009, p. 226). Nine villages or communities are within 
the national park, and 22 are in the integrated management natural 
area. Of the 31 communities, 3 are located in the Andean plateau zone. 
In the lowlands, two of the communities occupy the zone of valleys 
around the municipality of Apolo. Timber extraction occurs here 
(WorldLand Trust 2010, p. 1). In 2010, an additional 25,090 ha (62,000 
ac) of pristine tropical rainforest in Bolivia were protected, 
following a decision by an indigenous community to create a tourism 
refuge in the Sadiri rainforest (WorldLand Trust 2010, p. 6). Landless 
Andean farmers make a living in the lowlands, and they at times expand 
the agricultural frontier, increasing the risk of disease transmission 
between domestic animals and wildlife, bringing crops and domestic 
animals closer to wildlife predators, and increasing hunting pressure 
in surrounding forests (WCS 2009, p. 4).
    In summary, threats to the species' habitat in Bolivia include 
unsustainable land use practices, illegal logging, road building, and 
exploration activities for oil extraction, which are contributing to 
the erosion of Bolivia's ecosystems (MacLeod 2009, p. 6; ParksWatch 
2005, p. 1). Large tracts of primary forest remain in Bolivia, but it 
is likely that many of these will be subjected to logging and other 
pressures, such as extraction of non-timber forest products, 
particularly because forest products contribute to Bolivia's national 
exports (Byers and Israel 2008, p. vi). The Government of Bolivia is 
attempting to balance improving its economy with conservation 
initiatives, and some of its development initiatives may negatively 
impact this species' habitat. Despite protections in place, this 
species' habitat in Bolivia continues to experience these threats, and 
we expect these pressures to continue into the future.

Colombia

    In the past, human colonization, development, and exploration 
within the range of the species in Colombia were limited due to the 
exceptionally steep and high terrain of the Andes (Salaman et al. 2002, 
p. 160). However, researchers reported in 2004 that the Cauca River 
Canyon in northeastern Colombia, an area containing military macaws, 
was extensively deforested (Flor[eacute]z and Sierra 2004, p. 3). The 
main threats in the lowlands are the expansion of agriculture, 
particularly by small farmers in the middle altitude areas, and 
extractive activities such as hunting (including the removal of birds 
to sell as pets) and wood harvesting (Salaman et al. 2007, p. 89). As 
resources become scarcer in the lowlands, these pressures move upland. 
Associated with these farming practices is the use of livestock and the 
erosion caused by livestock grazing on steep slopes, as well as erosion 
due to cultivation.
    A 2010 report indicated that forest cover was largely continuous in 
Colombia, but deforestation had increased dramatically as of 2010 (FAO 
2010, pp. 22, 106). Deforestation rates in lowland moist forest on the 
foothills of the eastern Andes of Colombia are rapidly accelerating. 
Deforestation has increased from 1.4 percent (1961-1979) to 4.4 percent 
(1979-1988), and is correlated with increasing human population density 
(Salaman et al. 2007, p. 89; Vi[ntilde]a and Cavelier 1999, p. 31). 
Primary forest habitats throughout Colombia have undergone extensive 
deforestation. Vi[ntilde]a et al. (2004, pp. 123-124) used satellite 
imagery to analyze deforestation rates and patterns along the 
Colombian-Ecuadorian border (in the Departments of Putumayo and 
Sucumbios, respectively), finding that between 1973 and 1996, a total 
of 829

[[Page 59987]]

km\2\ (320 mi\2\) of tropical forests within the study area were 
converted to other uses. This corresponds to a nearly one-third total 
loss of primary forest habitat, or a nearly 2 percent mean annual rate 
of deforestation within the study area.
    Since the 1970s, the Colombian Government has encouraged road 
construction and colonization projects. The goal is to create links to 
the vast and undeveloped Amazonian region, and to open up the Llanos 
and Amazonian lowlands for utilization of their natural resources 
(Salaman et al. 2007, pp. 10, 89; Salaman et al. 2002, p. 160). In 
recent years, this species' habitat has come under increased pressure 
with the completion of the Mocoa-Bogot[aacute] highway, the proposed 
Puerto As[iacute]s-Florencia road, and the discovery and exploitation 
of petroleum and precious metals. All of these factors contribute to an 
escalation in human encroachment and associated impacts that degrade 
this species' habitat (Salaman et al. 2007, p. 10). The few remaining 
forest connections between the upper and lower slopes are under 
pressure, even where they are minimally protected.
    Five main routes link the lowlands from Colombia's high Andean 
interior to other areas. Infrastructure development on the eastern 
slope of the Andes in Colombia, as well as adjacent Ecuador, has also 
caused significant human population pressures and has led to much 
habitat degradation. Increased and improved access roads have led to 
the conversion of mature tropical forests for pasture lands, petroleum 
products exploitation, and coca plantations (Salaman et al. 2007, p. 
89). These road projects to link Colombia with Venezuela and Ecuador 
along the entire eastern base of the Andes have contributed to 
additional deforestation.
Serran[iacute]a de los Churumbelos National Park
    Currently, the Serran[iacute]a de los Churumbelos forest is almost 
entirely intact and is owned by the government (Salaman et al. 2007, 
pp. 10, 91-92). This mountain range has largely avoided the degree of 
human impact that other regions have suffered. However, this is 
changing rapidly due to mineral exploration (petroleum and precious 
metals) and natural resources (timber and rich organic soils for 
agriculture) demands. The Serran[iacute]a de los Churumbelos could 
become the focus of large-scale deforestation and colonization in the 
near future (Salaman et al. 2007, p. 89). Parque Natural Nacional Cueva 
de los Gu[aacute]charos provides some protection to the forests in this 
region although it is a small park (approximately 5,000 ha or 12,355 
ac), and even here, illegal encroachment occurs (Salaman et al. 2007, 
p. 89).
Catatumbo-Bar[iacute] National Park
    The primary threat in the Catatumbo-Bar[iacute] National Park (at 
the Colombian-Venezuelan border) is deforestation and impacts 
associated with coca plantations surrounding the Park (Fundaci[oacute]n 
ProAves 2011, pp. 28-29). Coca cultivation has fluctuated for several 
years. Over a 4-year study period, it contained about 100 ha (247 ac) 
of coca (United Nations Office on Drugs and Crime, undated report, p. 
33). A new population of this species was recently recorded at two 
locations in this park (Avenda[ntilde]o 2011 in BLI 2014a, p. 2). In 
addition, one population in the Cauca valley (fewer than 50 mature 
birds) could be affected by the construction of a dam (155 m (508.5 ft) 
in height) that could affect its sole breeding cliff. However, the 
status of the dam is still unclear (American Bird Conservancy 2012, p. 
24).

Ecuador

    Ecuador experiences one of the highest deforestation rates in South 
America (Mosandl et al. 2008, p. 37). Forested habitat within many 
parts of Ecuador has diminished rapidly due to logging, clearing for 
agriculture, and road development (Youth 2009, pp. 1-3; Mosandl et al. 
2008, p. 37; Sierra 1999, p. 136; Dodson and Gentry 1991, pp. 283-293). 
Between the years 1990 and 2005, Ecuador lost a total of 2.96 million 
ha (7.31 million ac) of primary forest, which represents a 16.7 percent 
deforestation rate, and a total loss of 21.5 percent of forested 
habitat since 1990 (Butler 2006b, pp. 1-3; FAO 2003b, p. 1). Much of 
the primary moist forest habitat has been replaced with pastures and 
scattered trees (Collar et al. 1992, p. 533). Very little suitable 
habitat now remains for the species here, and remaining suitable 
habitat is highly fragmented (Bass et al. 2010, p. 2; Snyder et al. 
2000, p. 122). In the area where this species exists, near the Gran 
Sumaco Biosphere Reserve, there are several oil reserves (Celi-
Sangurima 2005, p. 22). However, specific impacts to this species as a 
result of oil exploration or extraction activities are unknown.
    The colony in Kichwa River Reserve is currently in an area 
designated as protected, although it is unclear what these protections 
entail. In this area, the local community group Macaw Rio is interested 
in conducting ecotourism. Although this colony has persisted for about 
150 years (Huatatoca pers comm. in Arcos-Torres and Solano-Ugalde 2008, 
p. 72), it likely will be affected by logging and the resulting 
deforestation on nearby land. Researchers suggest that the apparent 
lack of this species in Ecuador is possibly related to lack of suitable 
sites for the formation of breeding colonies, or lack of knowledge 
about sites that may be located in inaccessible areas (Arcos-Torres and 
Solano-Ugalde 2008, p. 72). We know of no specific threats to the 
species in the Kichwa River Reserve, other than those associated with 
small population sizes, which is discussed under Small Population Size, 
below.

Mexico

    Mexico has suffered extensive deforestation (conversion of forest 
to other land uses) and forest degradation (reduction in forest biomass 
through selective cutting, etc.) over the past several decades 
(Commission for Environmental Cooperation (CEC) 2010, pp. 45, 75). In 
recent decades, Mexico's deforestation has been rapid (Blaser et al. 
2011, pp. 343-344). Between 1990 and 2000, Mexico lost forest 
(factoring in natural regeneration of degraded forest and planting of 
forest in areas that previously did not have forest) at a net rate of 
344,000 ha (850,043 ac) per year (FAO 2010, p. 21). During 1990-2010, 
Mexico lost approximately 6 million ha (15 million ac) of forest, and 
had one of the largest decreases in primary forests worldwide (FAO 
2010, pp. 56, 233). Although Mexico's rate of forest loss has slowed in 
the past decade, it still continues. The current rate of net forest 
loss in Mexico is 155,000 ha (383,013 ac) per year, with an estimated 
250,000-300,000 ha (617,763-741,316 ac) per year degraded (Government 
of Mexico (GOM) 2010b, in Blaser et al. 2011, p. 344; FAO 2010, p. 
233).
    As of 2010, Mexico had 64.8 million ha (160.1 million ac) of forest 
(Food and Agriculture Organization (FAO) 2010, p. 228), and 50 percent 
of these forests are considered degraded. Projections of lost forested 
area by the year 2030 in Mexico are between 10 percent to nearly 60 
percent of mature forests lost, and approximately 0 to 54 percent of 
regrowth forests lost (CEC 2010, pp. 45, 75). Deforestation via forest 
conversion to agricultural uses remains a major driver of land 
transformation in Mexico (CEC 2008, p. 24). Agricultural production is 
projected to double within the country by 2030 (CEC 2010, pp. 34, 70). 
Although some of this increase in production is expected due to an 
increase in productivity on previously converted land, total 
agricultural land area in Mexico is projected to increase by 6,300 to 
41,400 ha (15,568 to 102,302 ac) by 2030 (CEC 2010, p. 75).

[[Page 59988]]

    In the range of the military macaw, such as the tropical forest 
along the Pacific coast of Mexico, high rates of deforestation have 
occurred; slash-and-burn agriculture still occurs along with grazing. 
In 2002, it was estimated that the species had suffered a 23 percent 
habitat loss within its range in Mexico using a Genetic Algorithm for 
Rule-set Prediction (GARP) analysis tool (R[iacute]os-Mu[ntilde]oz 
2002, pp. 24, 32). GARP analysis essentially uses ecological 
characteristics of known species locations in order to determine its 
likely distribution.
    A 3-year study documented loss of habitat, particularly trees used 
by macaws, in the Tehuacan-Cuicatlan Biosphere Reserve, Sabino Canyon. 
In their study, researchers found a total of 170 individual plants of 
species consumed by military macaws in the pine forests in an area of 
1,500 m\2\ (16,146 ft\2\) in 2005 (Arizmendi 2008, p. 43). By January 
2008, eleven (6.5 percent) of these trees had been logged. In the 
transitional forest between dry and pine (in an area of 1,000 m\2\ or 
10,764 ft\2\), 134 plants were documented in 2005, and by January 2008, 
fifteen (11.90 percent) of them had been logged. Arizmendi suggested 
that these activities are carried out by local communities, and 
suggested that a local environmental education campaign be implemented. 
A reduced number of trees limit the availability of adequate food 
resources across the landscape. With fewer trees remaining, the area 
cannot support the same number of individuals of the species and, 
therefore, causes a further reduction in the population. Macaws were 
not found in deforested areas, even where one of their important food 
sources, Hura polyandra, was left as shade for cattle (Rivera-
Ort[iacute]z et al. 2008, p. 256). As further support, in Jalisco, most 
of the sites where macaws were present had little or no habitat loss 
(note that none of the sites in Jalisco where military macaws were 
located were in protected areas). No macaws were located in sites with 
more than 30 percent habitat loss, even though these sites may have had 
abundant trees.
Mining
    At the Mineral de Nuestra Se[ntilde]ora reserve in C[oacute]sala, 
where this species occurs, mining activities are occurring (Rubio et 
al. 2007, p. 52; Bonilla-Ruz et al. 2007b, p. 45). This reserve is 12 
km (7.5 mi) southeast of C[oacute]sala in Sinaloa, Mexico. This reserve 
was created after a joint effort in 1999 between the state, municipal 
government, and the Autonomous University of Sinaloa. The Autonomous 
University of Sinaloa conducted technical studies to propose the area 
as a nature reserve. The university also conducted conservation 
projects here which focused on the ``Ecology and Conservation of the 
Military Macaw'' and ``Environmental Education and Ecotourism.'' In 
2002, the Mineral de Nuestra Se[ntilde]ora reserve was formally 
designated. Since then, parrot populations and their habitat here both 
within and outside the preserve have been affected by mining activities 
taking place in the area (Rubio et al. 2007, p. 52). In early 2005, 
mining efforts began on underground development and drilling (Scorpio 
Mining 2011, p. 2). The current effect of mining on the species is 
unclear.

Peru

    There is little to no current published information with respect to 
specific threats to this species in Peru (Gasta[ntilde]aga et al. 2011, 
entire; JGP Consultants 2011, entire; Lee 2010, entire; Cowen 2009, 
entire; Terborgh 2004, entire; Brightsmith 2004, entire). It exists in 
several parks that convey some measures of protection (Oliveira et al. 
2007, p. 1,235; Terborgh 2004, p. 35). Peru's protected areas are 
managed by the General Department of Natural Protected Areas, INRENA, 
under the authority of Law No. 26834, Law of Natural Protected Areas, 
promulgated in 1997. The Peruvian national protected area system 
includes several categories of habitat protection. Habitat may be 
designated as any of the following:
    (1) Parque Nacional (National Park, an area managed mainly for 
ecosystem conservation and recreation);
    (2) Santuario (Sanctuary, for the preservation of sites of notable 
natural or historical importance);
    (3) Reserva Nacional (National Reserve, for sustainable extraction 
of certain biological resources);
    (4) Bosque de Protecci[oacute]n (Protection Forest, to safeguard 
soils and forests, especially for watershed conservation);
    (5) Zona Reservada (Reserved Zone, for temporary protection while 
further study is under way to determine their importance);
    (6) Bosque Nacional (National Forest, to be managed for 
utilization);
    (7) Reserva Comunal (Communal Reserve, for local area use and 
management, with national oversight); and
    (8) Cotos de Caza (Hunting Reserve, for local use and management, 
with national oversight) (BLI 2008, p. 1; Rodr[iacute]guez and Young 
2000, p. 330).
    Because the designations of national parks, sanctuaries, and 
protection forests are established by supreme decree that supersedes 
all other legal claim to the land, these areas tend to provide more 
habitat protection than other designations. All other protected areas 
are established by supreme resolution, which is viewed as a less 
powerful form of protection (Rodr[iacute]guez and Young 2000, p. 330).
    This species has been documented in the Tambopata National Reserve, 
which is a 275,000-ha (679,540-ac) conservation area created by the 
Peruvian Government in 1990. The main purpose was to protect the 
watersheds of the Tambopata and Candamo Rivers. This area protects some 
of the last pristine lowland and premontane tropical humid forests in 
the Amazon. Within the Tambopata National Reserve, there have been 
isolated human settlements along stretches of the Malinowski River, 
which flows into the Tambopata River. Fewer than 5,000 people inhabit 
the Tambopata National Reserve's border area to the north. They make a 
living of slash-and-burn agriculture, small-scale gold mining, timber 
extraction, and hunting and fishing. One area of Tambopata, including a 
buffer zone, was recently described as a ``crisis zone'' (Lee 2010, p. 
169). It has been described as being at high risk for illegal 
settlement, timber extraction, and mining (Lee 2010, p. 169).
    Populations of this species are thought to be in the Manu Biosphere 
Reserve and the Bahuaja Sonene National Park in Peru (WCS 2007, p. 1; 
Herzog in litt. 2007; Terborgh 2004, pp. 40-41). The problems here are 
primarily due to human population growth (Terborgh 2004, pp. 40-41). 
Five indigenous groups reside in the Manu Biosphere Reserve--they are 
both legal and illegal settlers (Terborgh 2004, pp. 40-41). An 
ecological research station has been in place since 1973 in Man[uacute] 
National Park (Terborgh 2004, entire), which also adds some protection 
to the species. Research has shown that often simply having a long-term 
research presence there can help to reduce poaching (Campbell et al. 
2011, p. 2). Unlike parks in the United States, in countries such as 
Peru, parks and protected areas were formed around the indigenous 
tribes that live there (Terborgh 2004, p. 51), and the management and 
purpose of the parks often include protection of the rights of 
indigenous human communities. This philosophy of park protection and 
mandates of parks differs from in the United States, where humans are 
viewed as visitors to the parks, rather than permanent residents 
(Terborgh 2004, p. 51). In Manu Biosphere Reserve, another potential 
threat is oil exploration. Both Shell and Mobil Oil

[[Page 59989]]

have conducted oil exploration activities in this area (Terborgh 2004, 
p. 55; ParksWatch 2002, pp. 5, 7). Within Bahuaja, as of 2002, there 
were no human establishments within its boundaries (ParksWatch 2002a, 
p. 1). However, activities that could affect the military macaw in this 
area include gold mining, illegal logging, extraction of forest 
resources, and farming (ParksWatch 2002b, p. 1).

Venezuela

    There is little published information about the military macaw in 
Venezuela (BLI 2014, pp. 1-2; Rodriguez 2004, entire). Here it exists 
in the Andes in the Central Coastal Cordillera, and Sierra de 
Perij[aacute] (Rodriguez et al. 2004, pp. 375, 378, 379). It has been 
found on the north slopes of El [Aacute]vila, Guatopo, Henri Pittier 
National Park, Ceroo La Mision, and Sierra de Perij[aacute] National 
Park (Desenne and Strahl 1994 in Snyder et al. 2000, p. 125; Fernandez-
Badillo et al. 1994 in Snyder et al. 2000 p. 125). Most of its range in 
Venezuela is within protected areas, but as of 2000, threats still were 
reported to exist in the protected areas (Snyder et al. 2000, p. 125). 
In 2000, Snyder et al. noted that Sierra de Perij[aacute] was being 
deforested for narcotics, land speculation, and cattle (p. 125). A 
population of this species was recorded for the first time at two 
localities at the Catatumbo-Bar[iacute] National Park in the Colombian-
Venezuelan border, extending the previous species' range from the east 
slope of the Serran[iacute]a de Perij[aacute] southwards 
(Avenda[ntilde]o 2011, p. 2).

Summary of Factor A

    Habitat loss, human encroachment, and conversion to agriculture are 
the main threats acting on the species throughout its range. These 
threats are exacerbated by an inability by range country governments to 
adequately manage and monitor the species (see discussion under Factor 
D, below). South America had the largest net loss of forest area of all 
continents between 2000 and 2005 (Mosandl et al. 2008, p. 38), with a 
net loss of 4.3 million ha per year. Although specific, detailed 
information about this species' remaining occupied habitat status is 
not available for each country, we know that much of this species' 
habitat has been lost through conversion of land to farming, forestry, 
or other activities (Bonilha and Switkes 2008, p. 17; Etter et al. 
2006, p. 369; Renton 2004, p. 13). Conversion of habitat to soy 
plantations is now considered to be one of the principal causes of 
Amazon deforestation. Deforestation may already have destroyed as much 
as 1.2 million ha (3 million ac) in the Amazon. This, combined with 
pressures of capture for the pet trade, has severely impacted the wild 
population of military macaws. Studies have shown that, over time, 
resident bird diversity generally declines as remaining forest becomes 
smaller and more fragmented (Turner 1996, pp. 202, 206).
    As with most parrots, the military macaw requires large areas of 
suitable habitat, including large trees or other nesting cavities for 
nesting, feeding, and roosting as well as food sources. Deforestation 
and logging is a common form of habitat loss that affects this species 
(Benetiz-Diaz 2012, p. 4; R[iacute]os-Mu[ntilde]oz et al. 2009, pp. 
502-505). Deforestation via conversion of land to agricultural use is a 
threat to military macaws because it directly eliminates forest 
habitat, removing the trees that support the species' nesting, 
roosting, and dietary requirements. It also results in fragmented 
habitat that isolates military macaw populations, potentially 
compromising the genetics of these populations through inbreeding 
depression and genetic drift (Lande 1995, pp. 787-789; Gilpin and 
Soul[eacute] 1986, p. 27). We do not know the exact extent of 
deforestation in the range of the military macaw. However, the best 
available information indicates that deforestation continues to occur 
and affect the species throughout its range, despite protections that 
are in place.
    Currently the population of military macaws is extremely small 
(likely a few thousand individuals), those populations are severely 
fragmented, and its suitable habitat is becoming increasingly more 
scarce. Therefore, based on the best available scientific and 
commercial information, we find that the present or threatened 
destruction, modification, or curtailment of habitat or range is a 
threat to the military macaw now and in the future.

B. Overutilization for Commercial, Recreational, Scientific, or 
Educational Purposes

    The trade in wild parrots is common in some areas of South America 
(Gasta[ntilde]aga et al. 2011, entire; Cant[uacute]-Guzm[aacute]n et 
al. 2008, entire). In its Red List assessment, the IUCN indicates that 
the two major threats to the military macaw are habitat loss and 
capture for the domestic pet trade (IUCN 2011, p. 1). Many reports 
indicate that poaching for the pet trade is still a problem for parrot 
species, particularly in poorer countries (Herrera and Hennessey 2007, 
entire; Dickson 2005, p. 548). For perspective, in the United States, 
captive-bred specimens of this species were recently found offered for 
sale for $699 (Basile 2010, p. 2). In 2006, four military macaws were 
advertised for sale with an average sale price of $850 (Cant[uacute]-
Guzm[aacute]n et al. 2008, p. 72). Although the scope of the illegal 
trade in the military macaw is unknown, poaching can be a lucrative and 
relatively risk-free source of income (Dickson 2005, p. 548).
    A high percentage of birds die during the process of capturing from 
the wild, transporting, and selling them. Because most of these 
activities are illegal, it is difficult to accurately determine the 
actual mortality rate, but estimates vary between 31 and 90 percent 
(Weston and Memon 2009, p. 79; Cant[uacute]-Guzm[aacute]n et al. 2007, 
pp. 7, 20, 22, 55, 60). Military macaws mate for life, are long-lived, 
and have low reproductive rates. These traits make them particularly 
sensitive to the impacts of their removal from the wild (Lee 2010, p. 
3; Thiollay 2005, p. 1,121; Wright et al. 2001, p. 711). Wild harvest 
can destroy pair bonds, remove potentially reproductive adults from the 
breeding pool, and have a significant effect on small populations 
(Kramer and Drake 2010, p. 11). These activities adversely affect a 
species' population numbers (Pain et al. 2006, p. 322).
    Although poaching continues to occur for the pet trade, it has been 
found to be significantly lower at protected sites (Pain et al. 2006, 
pp. 322-328; Wright et al. 2002, p. 719). Other reports have found that 
national or local protection, particularly when local communities are 
actively involved in conservation efforts, can successfully reduce nest 
take (Pain et al. 2006, p. 328; Chassot et al. 2006, pp. 86-87). 
Gonzalez (2003, pp. 437-446) found evidence of poaching, particularly 
during nesting seasons, in the Pacaya-Samiria National Reserve, a 
protected area in the Loreto Department, Peru, during his 1996-1999 
study. However, he also found that poaching decreased during the 1998 
harvest season (Gonzalez 2003, p. 444), which he attributed to 
increased numbers of birds confiscated by regional authorities, which 
may have subsequently discouraged poaching (also see Factor D, below).
    A related factor is the destruction of trees in this species' 
habitat due to poaching. This species primarily depends on tree-cavity 
nests as its habitat. Not only does nest poaching negatively affect 
this species by reducing the population size and the number of birds 
available to reproduce, it also in some cases destroys this species' 
habitat. Several studies have found that poachers will cut down trees 
to remove nests. A study conducted in the late 1990s found that in some 
cases

[[Page 59990]]

in Peru, poachers cut down the nesting tree in order to access the 
nestlings (Gonzalez 2003, p. 443). They also were observed ``hacking'' 
open the nest cavities to remove chicks (Bergman 2009, pp. 6-8; Low 
2003, pp. 10-11). An average of 21 nests was destroyed per poaching 
trip (Gonzalez 2003, p. 443). Nest destruction was also reported by 
Bergman in Ecuador in 2009 (pp. 6-8).
    The military macaw was listed in CITES Appendix II, effective June 
6, 1981, and was transferred to CITES Appendix I, effective October 22, 
1987. Most of the international trade in military macaw specimens 
consists of live birds. Data obtained from the United Nations 
Environment Programme--World Conservation Monitoring Center (UNEP-WCMC) 
CITES Trade Database show that, during the nearly 6 \1/2\ years that 
the military macaw was listed in Appendix II, a total of 1,034 military 
macaw specimens were reported to UNEP-WCMC as (gross) exports. Of those 
1,034 specimens, 1,019 were live birds and 15 were feathers. In 
analyzing these data, it appears that several records may be over-
counts due to slight differences in the manner in which the importing 
and exporting countries reported their trade. It is likely that the 
actual number of military macaw specimens in international trade during 
this period was 973, including 958 live birds and 15 feathers. Fourteen 
of the live birds were captive-bred, and the others were reported with 
the source unknown. Exports from range countries included: 364 live 
birds from Bolivia; 320 from Mexico; 11 from Ecuador; 4 from Venezuela; 
and 1 from Argentina.
    During the more than 25 years following the transfer to Appendix I 
(October 22, 1987 through December 31, 2012, the last year for which 
complete data were available at the time the following numbers were 
compiled, the UNEP-WCMC database shows a total of 1,894 military macaw 
specimens as (gross) exports, including 1,455 live birds, 224 
scientific specimens, 213 feathers, 1 body, and 1 trophy (UNEP-WCMC 
trade database, accessed May 20, 2014). As noted above, it appears that 
some records may be over-counts due to differences in the manner in 
which the importing and exporting countries reported their trade. It is 
likely that the actual number of live military macaws in international 
trade during the 25-year period was 1,301. Of those 1,301 birds, 1,022 
were captive-bred or captive-born, and 119 were reported as wild. The 
source of the remaining live birds is unknown. Exports from range 
countries included: 54 live birds from Mexico; 10 from Argentina; 4 
from Venezuela; 2 from Colombia; and 1 from Peru. Annual quantities 
exported ranged from a low of 14 live birds during 2006, to 122 live 
birds (including 80 exported from South Africa) in 2009. Since 2004, 
none of the exports from range countries has been reported as wild 
origin.

Argentina, Bolivia, Ecuador, and Mexico

    In Argentina, Ecuador, and Venezuela, there is little to no 
information available about overutilization. International trade has 
diminished, but local trade continues to occur. In Bolivia, a report 
published in 2009 indicated that of 17,609 birds (including military 
macaws) documented in the market studied in Department of Santa Cruz 
(not far from the range of this species), 64 percent of the birds were 
found to be adults captured in the wild. Ninety percent (24,707) of the 
birds were found to be from the Department of Santa Cruz. A total of 
2,604 individuals were from the Department of Tarija, 176 from the 
Department of Beni, 20 from Peru, and 12 from Brazil (Herrera and 
Hennessey 2009, p. 233). The report indicated that most parrots (some 
of which were military macaws) were locally sold, and found that 23,306 
were in the city of Santa Cruz, and 4,156 were sent to Cochabamba.
    In Mexico, the military macaw is reportedly one of the most sought-
after species in the illegal pet bird trade (Cant[uacute]-Guzm[aacute]n 
et al. 2007, p. 38), and poaching remains a concern. In 1995-2005, it 
was the fifth most seized Mexican psittacine species by Mexico's 
Environmental Enforcement Agency, becoming the fourth most seized 
psittacine species in 2007-2010 (p. 52). As an example, at a sinkhole 
in El Cielo Biosphere Reserve, a population of approximately 50 birds 
was decimated by poaching in the 1980s (Arag[oacute]n-Tapia in litt. 
1989 in Snyder et al. 2000, p. 125). In many areas, it nests in 
relatively inaccessible cavities on cliff walls, which provide some 
protection against the pressures of nest poaching. However, nest 
poaching is a severe threat in Jalisco and Nayarit, where the species 
nests in tree cavities (Contreras-Gonz[aacute]lez et al. 2007, p. 43; 
Renton in litt. 2007 and Bonilla in litt. 2007 in BLI 2011a, pp. 1-2). 
Between 2005 and 2006 in Mexico, five military macaws were found for 
sale, and the average price was $373 (Cant[uacute]-Guzm[aacute]n et al. 
2007, p. 76).
    Local residents in Argentina indicated that young chicks are 
removed ``for foreigners'' but also noted that it is extremely 
difficult due to the difficulty in accessing the species' preferred 
nesting sites and the aggressiveness of the macaws (Navarro et al. 
2008, pp. 7, 9). Additionally, in Mexico and Ecuador, indigenous 
communities have used military macaw feathers for ceremonial and 
medicinal practices. However, NGOs are working with these communities 
to obtain macaw feathers from aviaries so that the indigenous people 
will not hunt the macaws (Renton 2004, p. 14).

Colombia

    This species and other Ara macaws are occasionally hunted by 
indigenous people in Colombia. In one study, in the Catatumbo-
Bar[iacute] National Park, hunting was found to be concentrated around 
the 15 indigenous communities within the 160,000-ha (395,369-ac) park 
(Avenda[ntilde]o 2011, p. 2). In 2004, in a cliff-nesting location 
along the Cauca River, Colombia, threats to this species included 
poaching and loss of foraging trees (Fl[oacute]rez and Sierra 2004, pp. 
2-3). They found that, at the Cauca River site, it was common for some 
people to remove hatchlings from the nests and sell between 20 to 30 
chicks per year on the black market (p. 3). To counteract these 
activities, a local awareness campaign was initiated (Fl[oacute]rez and 
Sierra 2004, pp. 2-3). As a result of this project, 3,000 Hura 
crepitans trees (a species used by the military macaw) were planted by 
the local communities, and the awareness campaign appeared to be 
effective. Researchers do not believe that hunting pressure is a 
serious short-term threat. However, local education and awareness 
programs generally need to be ongoing and long-term for them to be 
effective, and the local communities need to be aware of the benefits 
of conserving species in the wild as well as having an alternative 
source of income (i.e., income other than that derived from poaching).

Peru

    A recent study in Peru examined nest poaching and illegal trade of 
parrots, including the reasons for poaching, and the methods, seasons, 
and locations where the sale and actual poaching of parrots occurred. 
This study found that this species is still being poached in the wild 
(Gasta[ntilde]aga et al. 2011, pp. 79-80), even in protected areas and 
despite national protections in place. During the 2007-2008 study, 
eight military macaws were found for sale in two out of eight markets 
surveyed in Peru (p. 79). Seven of these birds were found in the 
Amazonian lowland city, Pucallpa (p. 80). The study also found that, 
where protections and enforcement have been implemented such as in 
Cusco, there were no parrots for sale in markets. This

[[Page 59991]]

indicates that, although it still continues, poaching is becoming less 
frequent due to involvement by NGOs, minimal international demand for 
the species, and enforcement by authorities.

Summary of Factor B

    Among birds, parrots are the group most subject to commercial trade 
(Hutton et al. 2000, p. 14). Parrots have suffered a disproportionate 
number of extinctions, in part due to their desirability as pets. 
Conservation efforts by the various entities working to ensure long-
term conservation of the military macaw may result in its population 
slowly increasing; however, it is likely that the population is still 
declining. Even though the military macaw is listed as an Appendix-I 
species under CITES and laws have been established within the range 
countries to protect this species, we are still concerned about the 
illegal capture of this species in the wild. Despite regulatory 
mechanisms in place and restricted international trade, poaching is 
lucrative and continues to occur. Additionally, because each population 
of military macaws is small, with usually fewer than 100 individuals, 
poaching is likely to have a significant effect on the species. Based 
on the best available scientific and commercial information, we find 
that overutilization for commercial, recreational, scientific, or 
educational purposes is a threat to the military macaw throughout its 
range.

C. Disease or Predation

Disease

    Studies of macaws indicate that this species is susceptible to many 
bacterial, parasitic, and viral diseases, particularly in captive 
environments (Kistler et al. 2009, p. 2,176; Portaels et al. 1996, p. 
319; Bennett et al. 1991). Viral diseases seem to be more prevalent and 
subsequently more studied in parrots than bacteria and parasites. 
Psittacines are prone to many viral infections such as retrovirus, pox 
virus, and paramyxo virus, and captive-held birds seem particularly 
susceptible (Gaskin 1989, pp. 249, 251, 252). A highly fatal disease, 
Pacheco's parrot disease, is also caused by a virus (Simpson et al. 
1976, p. 218). After infection from this virus, death occurs suddenly 
without apparent sign of sickness other than some mild nasal discharge 
and lethargy (Simpson et al. 1976, p. 211). However, as transmission of 
this disease is mainly through nasal discharge and feces, it is less 
likely to happen in open habitat in the wild than in a confined aviary, 
particularly because in the wild this species has been observed to 
alternate nest sites based on food availability (Chosset et al. 2004, 
pp. 35-39). Another disease, proventricular dilatation disease (PDD), 
may be one of the worst diseases known to affect parrots (Kistler et 
al. 2008, p. 2). PDD has been documented in several continents in more 
than 50 different parrot species and in free-ranging species in at 
least five other orders of birds (Kistler et al. 2008, p. 2). It is not 
clear if some diseases observed in birds in captivity also occur in the 
wild with the same frequency. However, because the populations of 
military macaws are small and widely distributed, disease is less of a 
concern because diseases tend to be more easily transmitted between 
individuals within close range, and wild birds disperse and are not 
constantly in close proximity. Also, captive conditions in aviaries 
make birds more susceptible to disease where the stress of confinement 
combined with inadequate diet can reduce the ability of birds to fight 
disease.
    We have no evidence of significant adverse impacts to wild 
populations of military macaws due to disease. Disease is a normal 
occurrence within wild populations. There is no indication that disease 
occurs to an extent that it is a threat. Based on the best available 
scientific and commercial information, we find that disease is not a 
threat to the military macaw in any portion of its range now or in the 
future.

Predation

    Eggs and chicks are more susceptible to predation than adult macaws 
(Arizmendi 2008, p. 44). Chicks and eggs are particularly susceptible 
to predation by snakes (Arizmendi 2008, p. 44), but military macaws 
select their nests where they are likely to have a high level of 
reproductive success. Because military macaws generally construct their 
nests in high locations such as canyon cliffs, snake predation is less 
of a concern because snakes need tree canopy or vines to climb in order 
to gain access to eggs and chicks.
    Other predators known to consume this species' eggs include 
iguanas, red-tailed hawks (Buteo jamaicensis), turkey vultures 
(Carthates aura), and some mammals (Arizmendi 2008, p. 44). In the 
Sabino canyon, iguanas were observed near the nesting sites. 
Researchers suggested that a predator control program here would 
benefit the macaws (Arizmendi 2008, p. 45). Macaws frequently exhibit 
alarmed behavior when red-tailed hawks and turkey vultures approach 
their nests (Arizmendi 2008, p. 44). In Argentina, a flock of parrots 
was attacked by a pair of peregrine falcons (Falco peregrinus), which 
also nest in ravines (Navarro et al. 2008, p. 6). However, although 
parrots and falcons can be combative, the peregrine falcon, which 
normally consumes small mammals and birds, is not thought to be a 
natural predator of the military macaw (Bradley et al. 1991, p. 193). 
Due to its large size and careful nest site selection, the military 
macaw is less susceptible to predation by both land and aerial 
predators (Flor[eacute]z and Sierra 2004, pp. 2-3). However, even 
limited predation is still a concern in part because removal of 
potentially reproductive adults from the breeding pool can have a 
significant effect on small populations by destroying macaw mating pair 
bonds (Kramer and Drake 2010, p. 11). Additionally, studies on similar 
species in similar Andean habitats indicate that vulnerability to 
predation by generalist predators increases with increased habitat 
fragmentation and smaller patch sizes (Arango-V[eacute]lez and Kattan 
1997, p. 140). Because each population of military macaws is small, 
with usually fewer than 100 individuals, and because this species mates 
for life, even low levels of predation are likely to have a significant 
effect on the species.

Summary of Factor C

    Diseases associated with military macaws in the wild are not well 
documented. Although there is evidence that diseases occur in parrots 
in the wild, we found no information that diseases affect this species 
to the degree that they are negatively impacting this species in the 
wild. Because the populations are distributed across such a large area, 
these populations have resiliency against impacts from disease if one 
population is affected by a disease outbreak. Conversely, although 
disease in the wild is not a concern, predation does remain a concern; 
there is evidence that predation on this species occurs often enough 
that it can have a significant impact. Because of the species' small 
and declining population size, tendency to mate for life, low 
reproductive capacity, and existence in isolated habitat fragments, 
even minimal predation renders the species more vulnerable to local 
extirpations. Therefore, we find that predation, compounded by ongoing 
habitat loss and poaching, is a threat to the military macaw.

D. The Inadequacy of Existing Regulatory Mechanisms

    Regulatory mechanisms to protect a species could potentially fall 
under categories such as regulation of trade, wildlife management, 
parks

[[Page 59992]]

management, or forestry management. Regulatory mechanisms could be at 
the local, national, or international levels.

International Wildlife Trade (CITES)

    A specimen of a CITES-listed species may be imported into or 
exported (or reexported) from a country only if the appropriate permit 
or certificate has been obtained prior to the international trade and 
it is presented for clearance at the port of entry or exit. The 
Conference of the Parties (CoP), which is the decisionmaking body of 
the Convention and comprises all its member countries, has agreed on a 
set of biological and trade criteria to help determine whether a 
species should be included in Appendix I or II. The military macaw is 
listed in Appendix I. For Appendix-I species, both an export permit (or 
reexport certificate) must be issued by the country of export and an 
import permit from the country of import must be obtained prior to 
international trade. An export permit for species listed in either 
Appendix I or II may only be issued if the country of export determines 
that:
     The export will not be detrimental to the survival of the 
species in the wild (CITES Article III(2) and Article IV(2));
     The specimen was legally obtained according to the animal 
and plant protection laws in the country of export;
     For live animals or plants, they are prepared and shipped 
for export to minimize any risk of injury, damage to health, or cruel 
treatment; and
     For Appendix I species, an import permit has been granted 
by the importing country.
    Except in certain cases, such as specific scenarios for approved 
captive-breeding programs, the import of an Appendix-I species requires 
the issuance of both an import and export permit. Import permits are 
issued only after the importing country determines that it will not be 
used for primarily commercial purposes (CITES Article III(3)) and that 
the proposed recipient of live animals or plants is suitably equipped 
to house and care for them. Thus, with few exceptions, Appendix-I 
species cannot be traded for commercial purposes.
    The CITES Treaty requires Parties (member countries) to have 
adequate legislation in place for its implementation. Under CITES 
Resolution Conference 8.4 (Rev. CoP15) and related decisions of the 
CoP, the National Legislation Project evaluates whether Parties have 
adequate domestic legislation to successfully implement the Treaty 
(CITES 2011a). In reviewing a country's national legislation, the CITES 
Secretariat evaluates factors such as:
     Whether a Party's domestic laws prohibit trade contrary to 
the requirements of the Convention,
     Whether a Party has penalty provisions in place for 
illegal trade, and if they have designated the responsible Scientific 
and Management Authorities, and
     Whether a Party's legislation provides for seizure of 
specimens that are illegally traded or possessed.
    The CITES Secretariat has determined that the legislation of 
Argentina, Colombia, Mexico, and Peru is in Category 1, meaning they 
meet all the requirements to implement CITES. Bolivia, Ecuador, and 
Venezuela were determined to be in Category 2, with a draft plan, but 
not enacted (http://www.cites.org, SC62 Document 23, pp. 7-8). This 
means the Secretariat determined that the legislation of Bolivia, 
Ecuador, and Venezuela meet some, but not all, of the requirements for 
implementing CITES. Based on the decrease in reported international 
trade, CITES and the range countries for this species have effectively 
controlled legal international trade of this species. Therefore, we 
find CITES is an effective mechanism for preventing overexploitation 
for international trade in this species.

Parks and Habitat Management

    We are focusing our evaluation of the potential threats to this 
species primarily to parks for the following reasons. Most suitable 
habitat, primary forest, only remains in these protected areas. The 
best available information suggests that this species is now mostly 
found in protected areas such as parks, in part because this is where 
suitable habitat remains for the species. Additionally, the majority of 
the information available regarding the potential threats to the 
species pertains to the parks, where the species is usually found. Our 
rationale is supported by Cowen, who noted that encounter rates for 
large macaw species were generally higher in primary forests (2008, p. 
15), which tend to be located in areas with protected status. 
Throughout this species' range, we found that many of the threats that 
occur to this species are the same or similar. Threats generally 
consist of various forms of habitat loss or degradation. Each range 
country for this species has protections in place, but for reasons such 
as limited budgets and limited enforcement capabilities, the laws and 
protections are generally not able to adequately protect the species.
    Research has found that tropical parks have been surprisingly 
effective at protecting ecosystems and species within boundaries 
designated as parks or other protected status despite underfunding and 
pressures for resources (Oliveira et al. 2007, p. 1,235; Bruner et al. 
2001, p. 126; Terborgh 1999, entire). Bruner's study found that 
protected areas are especially effective in preventing land clearing. 
It found that, in 40 percent of parks, land that had formerly been 
under cultivation and that was incorporated into park boundaries had 
actually recovered. This subsequently led to an increase in vegetative 
cover. The study also found that 83 percent of parks were successful at 
mitigating encroachment (Bruner et al. 2001, p. 125). It concluded that 
the conditions inside the parks were significantly better than in their 
surrounding areas (Bruner et al. 2001, p. 125). Oliveira et al. found 
that forests in conservation units were four times better at protecting 
against deforestation than unprotected areas (2007, p. 1,235). However, 
despite these protections, this species has experienced threats such 
that their populations are now so small (generally fewer than 100 in 
each population) that any pressure now has a more significant effect. 
Parks, without management, are often insufficient to adequately protect 
the species. Our analysis of regulatory mechanisms is discussed 
essentially on a country-by-country basis, beginning with Argentina, 
and is summarized at the end. Conditions in specific parks are 
discussed below.

Argentina

    In 2007, Argentina enacted a law mandating minimum standards for 
the environmental protection of native forests (Ley de Bosques). 
However, the federal government has not fully enforced the law, and 
provincial governments are not in full compliance with it (DiPaola et 
al. 2008, p. 2). Argentina lacks adequate protections of its natural 
environments; there is a lack of environmental awareness and commitment 
from the government to adequately protect its resources (FAO 2007, pp. 
43-44, 59-60). Provinces usually allow landowners to decide whether to 
maintain forest cover or deforest the land. The absence of a serious 
land use planning strategy, particularly during the past 20 years, has 
led to significant habitat degradation (FAO 2007, p. 60). The threat to 
native forests has remained particularly high in the Salta Province. As 
a result, a coalition of indigenous communities and nongovernmental 
organizations filed for injunctive relief

[[Page 59993]]

in Argentina's highest court to attempt to combat deforestation 
(DiPaola et al. 2008, p. 2). In this case, the court mandated 
deforestation activities to be halted pending the completion of a 
cumulative environmental impact study. The decision forced the Salta 
Province to comply with the deforestation moratorium imposed by the 
Forestry Law, and pressured the Province to comply with the other key 
provision of the law by completing an environmental land use plan 
(DiPaola et al. 2008, p. 2). Although the Forestry Law is in place and 
the court case has set a precedent for compliance with this law, the 
area where this species occurs in Argentina to the best of our 
knowledge remains largely unprotected (Navarro et al. 2008, pp. 7, 9).

Bolivia

    This species primarily inhabits the parks and protected areas in 
Bolivia's Andean region (Herzog 2011, pers. comm.). National parks are 
intended to be strictly protected; however, some areas where the 
species occurs are also designated as areas of integrated management, 
which are managed for both biological conservation and the sustainable 
development of the local communities. Bolivia attempts to balance 
natural resource uses; however, it is one of the poorest countries in 
South America (MacLeod 2009, p. 6; CIA World Factbook, accessed 
December 6, 2011), and subsequently has competing priorities. As of 
2005, Bolivia had 5 national parks, 6 national park and integrated 
management natural areas, 1 national park and indigenous territory (or 
communal lands), 4 national reserves, 2 biosphere reserves, and 3 
integrated management natural areas (ParksWatch 2005, p. 1). These make 
up Bolivia's National System of Protected Areas ((SNAP) Servicio 
Nacional de Areas Protegidas). Below are the designations and their 
relevant categorizations of protections (eLAW 2003, p. 3).
    (1) Park, for strict and permanent protection of representative 
ecosystems and provincial habitats, as well as plant and animal 
resources, along with the geographical, scenic and natural landscapes 
that contain them;
    (2) Sanctuary, for the strict and permanent protection of sites 
that house endemic plants and animals that are threatened or in danger 
of extinction;
    (3) Natural Monument, to preserve areas such as those with 
distinctive natural landscapes or geologic formations, and to conserve 
the biological diversity contained therein;
    (4) Wildlife Reserve, for protection, management, sustainable use, 
and monitoring of wildlife;
    (5) Natural Area of Integrated Management, where conservation of 
biological diversity is balanced with sustainable development of the 
local population; and
    (6) ``Immobilized'' Natural Reserve, a temporary (5-year) 
designation for an area that requires further research before any 
official designations can be made and during which time no natural 
resource concessions can be made within the area (Supreme Decree No. 
24,781 1997, p. 3).
    The foundation of Bolivia's laws is largely based on Bolivia's 1975 
Law on Wildlife, National Parks, Hunting, and Fishing (Decree Law No. 
12,301 1975, pp. 1-34), which has the fundamental objective of 
protecting the country's natural resources. This law governs the 
protection, management, utilization, transportation, and selling of 
wildlife and their products; the protection of endangered species; 
habitat conservation of fauna and flora; and the declaration of 
national parks, biological reserves, refuges, and wildlife sanctuaries, 
regarding the preservation, promotion, and rational use of these 
resources (Decree Law No. 12,301 1975, pp. 1-34; eLAW 2003, p. 2). 
Later, Bolivia passed an overarching environmental law in 1992 (Law No. 
1,333 1992), with the intent of protecting and conserving the 
environment and natural resources. Studies have shown that protected 
areas have been successful in providing protection from poaching, 
logging, and other forest damage, especially when compared to 
unprotected areas (Lee 2010, p. 3; Killeen et al. 2007, p. 603; 
Oliveira et al. 2007, p. 1,234; Asner 2005, p. 480; Ribeiro et al. 
2005, p. 2; Gilardi and Munn 1998, p. 641). However, pressures on the 
parks' resources are increasing; these are described below.
    Within the Greater Madidi-Tambopata Landscape, activities that 
could negatively affect this species occur, and there are competing 
priorities within these protected areas. The GMTL is divided into three 
contiguous areas, with two different management categories: A strictly 
protected National Park in two sections that total 1,271,000 ha 
(3,140,709 ac), and a natural integrated management area with 624,250 
ha (1,542,555 ac), where conservation and sustainable development of 
the local communities is the main purpose (Conservation Strategy Fund 
(CSF) 2006, p. 29). The most significant activities that are having a 
negative impact or could in the future in this area are the 
construction of a highway within Madidi, mining for natural resources 
such as gold, drilling for oil, and a planned hydroelectric dam 
(ParksWatch 2011b, p. 8; http://www.amazonfund.eu/art-oil-madidi.html, 
accessed September 13, 2011; Chavez 2010, pp. 1-2). There is limited 
legal hunting of this species occurring here, but in the areas 
surveyed, this species was described as common and not exploited 
(Hosner et al. 2009, p. 226). Timber extraction still occurs in some 
areas (WorldLand Trust 2010, p. 1). In the rainforest and foothill 
forest of Serran[iacute]a Sadiri within Madidi, roads in the late 1990s 
spurred a rise in the unsustainable logging of the area's mahogany 
trees, which were the most valuable tree at the time (World Land Trust 
2010, pp. 1-2). Within the Apolobamba protected area, uncontrolled 
clearing, extensive agriculture, grazing, and ``irresponsible'' tourism 
are ongoing (Auza and Hennessey 2005, p. 81). Habitat degradation and 
destruction from grazing, forest fires, and timber extraction are 
ongoing in other protected areas, such as Tunari National Park 
(Department of Cochabamba), where suitable habitat exists for this 
species (De la Vie 2004, p. 7).
    Bolivia's national policy is to decentralize decisionmaking, and 
responsibility for land planning and natural resource management is 
increasingly shifting to local and regional governments (Wildlife 
Conservation Society (WCS) 2009, pp. 2-5). However, the 
decentralization process is occurring without sufficient personnel, 
staff training, and operational funds. There is little information as 
to the actual protections that Bolivia's laws and protected areas 
confer to military macaws, despite the laws in place at the national 
level for its wildlife. Threats to the species and its habitat include 
unsustainable land use practices, illegal logging, mining, road 
building, oil extraction, illegal animal trade, and hunting, which are 
all still occurring within this species' habitat (MacLeod 2009, p. 6; 
WCS 2009, pp. 2-5). The mechanisms in place are inadequate at reducing 
the threat of habitat destruction and human disturbance within these 
protected areas.

Colombia

    The Colombian Government has enacted and ratified numerous domestic 
and international laws, decrees, and resolutions for managing and 
conserving wildlife and flora. Colombia currently has 54 areas that 
have protected status (El Sistema Nacional de Areas

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Protegidas (SINAP); National Natural Parks of Colombia 2011). Of those, 
33 have been declared Important Bird Areas (IBAs). The protected area 
designations are as follows: national parks (parques nacionales), flora 
and fauna sanctuaries (santuarios de fauna y flora), flora sanctuaries 
(santuarios de flora), nature reserves (reserva natural), and unique 
natural areas ([aacute]rea natural [uacute]nica) (Law 165 of 1994). 
Small populations of this species occur in several reserves and 
protected areas in Colombia (Strewe and Navarro 2003, p. 32). These 
protected areas in Colombia offer various degrees of protection to the 
species.
    In 2003, conservation priorities were identified for its bird 
species, a conservation corridor was designed, and a habitat 
conservation strategy within the San Salvador valley was developed 
(Strewe and Navarro 2003, p. 29). The private Buena Vista Nature 
Reserve was established and protects approximately 400 ha (988 ac) of 
tropical wet lowland forest and wet premontane forest on the northern 
slope of the Sierra Nevada. It encompasses extensive primary forests 
along an altitudinal gradient of 600 to 2,300 m (1,968 to 7,545 ft) and 
forest patches and secondary forest at elevations between 450 to 600 m 
(1,476 to 1,968 ft). The reserve is adjacent to the Sierra Nevada de 
Santa Marta National Park and the Kogi-Malayo Indian reserve (Strewe 
and Navarro 2003, p. 29).
    A conservation project focusing on the coffee zone of the middle 
R[iacute]o Fr[iacute]o is ongoing, and its goal is to create a 
conservation corridor connecting natural habitats and shade-grown 
coffee plantations (Strewe and Navarro 2004, p. 51). The establishment 
of the private nature reserve, Buena Vista, was the first step to 
conserve the foothill forest ecosystems. This was done in close 
cooperation with a local organization, Grupo Ecologico Defensores de la 
Naturaleza-Campesinos de Palomino (Strewe and Navarro 2003, pp. 34-35). 
The Pro-Sierra Nevada de Santa Marta Foundation (FPSNSM) maintains a 
permanent monitoring station at Buena Vista nature reserve. FPSNSM is 
working toward sustainable development projects in cooperation with 
local communities, national park units, and coffee-grower committees in 
the region. This includes educational campaigns to limit hunting. 
Habitat management takes place on private lands in the lowlands and 
foothills of the San Salvador valley to reduce the pressure on the 
remaining natural forest habitats, including a reforestation program 
using native tree species. Additionally, forest reserves have been 
established as part of a network of private nature reserves in the 
valley (Strewe and Navarro 2003, pp. 35-36).
    Resource management in Colombia is highly decentralized. Colombian 
environmental management has been divided between the national and 
regional levels since the 1950s. Governmental institutions responsible 
for oversight appear to be under resourced (ITTO 2006, p. 222) and 
unable to adequately manage species such as the military macaw. 
Resources are managed within local municipalities by one of 33 
``Autonomous Regional Corporations'' known as CARs (Corporaciones 
Aut[oacute]nomas Regionales) (Blackman et al. 2006, p. 32). CARs are 
described as corporate bodies of a public nature, endowed with 
administrative and financial autonomy to manage the environment and 
renewable natural resources, implemented through Law 99 of 1993 (p. 
32). Each department (analogous to U.S. state designations) within 
Colombia is managed by a separate local entity. These corporations 
grant concessions, permits, and authorizations for forest harvesting 
(ITTO 2006, p. 219).
    As of 2005, 40 percent of Colombia's public resources were managed 
by local municipalities, making Colombia one of the most decentralized 
countries in terms of forestry management in Latin America (Blackman et 
al. 2006, p. 36). Monitoring of resource use and forest development 
authorized by these corporations is conducted mostly by local 
nongovernmental organizations. The International Tropical Timber 
Organization (ITTO) considers the Colombian forestry sector to be 
lacking in law enforcement and on-the-ground control of forest 
resources, with no specific standards for large-scale forestry 
production, no forestry concession policies, and a lack of transparency 
in the application of the various laws regulating wildlife and their 
habitats (ITTO 2006, p. 222). Consequently, there is currently no 
effective vehicle for overall coordination of species management for 
multijurisdictional species such as the military macaw. 
Fundaci[oacute]n ProAves developed a conservation plan for 2010 to 2020 
for several parrot species, including the military macaw (Botero-
Delgadillo and P[aacute]ez 2011, p. 7). However, it is unclear if or 
when it will be adopted by the Government of Colombia.
    Additionally, despite protections, forest loss continues almost 
unabated in the mountains of the Sierra Nevada, demonstrating that 
formal protections and regulatory mechanisms are inadequate. In this 
area, El Congo Reserve currently may be the only secure nesting site 
for the military macaw, but it is too small (40 ha; 99 ac) to conserve 
viable populations.
    Efforts are occurring in Colombia to protect and monitor its 
species, although they do not appear to be adequate to combat the 
threats to this species. One management tool that Colombia has recently 
developed is a bird-watching strategy in these protected areas to 
monitor and report on bird species such as the military macaw, in 
conjunction with ecotourism (National Natural Parks of Colombia 2011). 
Despite the efforts in place, there is a lack of information available 
about the status of this species and its habitat in Colombia. There is 
no clear information about the status of the species in Colombia, 
particularly its population trend. We are unable to determine that this 
conservation strategy will sufficiently mitigate threats to the 
military macaw, nor are we able to find that the regulatory mechanisms 
in place in Colombia are adequate. The species population is small in 
Colombia, and threats to its habitat still exist.

Ecuador

    In Ecuador, the military macaw is considered to be very rare 
(Arcos-Torres and Solano-Ugalde 2008, p. 72). It has been observed in 
the areas of Sumaco and Zamora-Chinchipe (Youth 2009, p. 1; Snyder et 
al. 2000, p. 125) and recently at Kichwa River Reserve (Reserva Kichwa 
R[iacute]o), within the Gran Sumaco Biosphere Reserve Guacamayos 
(Arcos-Torres and Solano-Ugalde 2008, p. 72). This species is 
categorized as endangered ``en peligro de extinci[oacute]n'' (Arcos-
Torres and Solano-Ugalde 2008, p. 69) in Ecuador. It is protected by 
Decree No. 3,516 of 2003 (Unified Text of the Secondary Legislation of 
the Ministry of Environment) (EcoLex 2003b, pp. 1-2 and 36). This 
decree summarizes the laws governing environmental policy in Ecuador 
and provides that the country's biodiversity be protected and used 
primarily in a sustainable manner.
    Habitat destruction is ongoing and extensive in Ecuador (Mosandl et 
al. 2008, p. 37; Butler 2006b, pp. 1-3; FAO 2003b, p. 1). Unsustainable 
forest harvest practices likely continue to impact the military macaw's 
habitat. In 2004, Ecuador Law No. 17 (Faolex 2004, pp. 1-29) amended 
the Forest Act of 1981 (Law No. 74) to include five criteria for 
sustainable forest management: (i) Sustainable timber production; (ii) 
the maintenance of forest cover; (iii) the conservation of 
biodiversity; (iv) co-responsibility in

[[Page 59995]]

management; and (v) the reduction of negative social and environmental 
impacts (ITTO 2006, p. 225; Aguilar and Vlosky 2005, pp. 9-10). In 
2001, the Ecuadorian Government worked with the private sector to 
develop a system of monitoring and control of forest harvest practices. 
However, in 2003, the Supreme Court of Ecuador declared the control 
system unconstitutional, and new control systems were being developed 
(ITTO 2006, p. 225). Approximately 70 percent of the forest products 
harvested are harvested illegally, or are used as fuel wood, or are 
discarded as waste (ITTO 2006, p. 226; Aguilar and Vlosky 2005, p. 4). 
Because the extractive harvesting industry is not monitored, the extent 
of the impact is unknown; however, the best available information 
indicates that habitat degradation negatively affects this species in 
Ecuador.
    The Ecuadorian Government recognizes 31 different legal categories 
of protected lands (e.g., national parks, biological reserves, geo-
botanical reserves, bird reserves, wildlife reserves, etc.). The colony 
in Kichwa River Reserve Macaw receives some legal protections by being 
in a Reserve. However, a study published in 2002 concluded that, 
although 14 percent of Ecuador is categorized as national reserve 
network (Sierra et al. 2002, p. 107), the system does not provide 
adequate protection for its ecosystems. As of 2006, the amount of 
protected land (both forested and nonforested) in Ecuador totals 
approximately 4.67 million ha (11.5 million ac) (ITTO 2006, p. 228). 
However, only 38 percent of these lands have appropriate conservation 
measures in place to be considered protected areas according to 
international standards (i.e., areas that are managed for scientific 
study or wilderness protection, for ecosystem protection and 
recreation, for conservation of specific natural features, or for 
conservation through management intervention) (IUCN 1994, pp. 17-20). 
The ITTO, as of 2006, considered ecosystem management and conservation 
in Ecuador, including effective implementation of mechanisms that would 
protect the military macaw and its habitat, to be lacking (ITTO 2006, 
p. 229).
    Although this colony has persisted for about 150 years (Huatatoca, 
pers. comm. in Arcos-Torres and Solano-Ugalde 2008, p. 72), it may be 
affected by logging and the resulting deforestation on nearby land 
(Arcos-Torres and Solano-Ugalde 2008, p. 72). The best available 
information indicates that on-the-ground enforcement of Ecuador's laws, 
oversight of the local jurisdictions, and implementing and regulating 
activities are ineffective in conserving the military macaw and its 
habitat in Ecuador. Researchers suggest that the apparent lack of this 
species in Ecuador is related to lack of existing suitable sites (large 
areas containing appropriate feeding, nesting, and breeding habitat) 
for the formation of breeding colonies. The governmental institutions 
responsible for natural resource oversight in Ecuador appear to be 
under-resourced, and to our knowledge, there is a lack of law 
enforcement on the ground. Despite the creation of a national forest 
plan, the best available information indicates there is a lack of 
capacity to implement this plan due to inconsistencies in application 
of regulations, and discrepancies between actual harvesting practices 
and forestry regulations. These inadequacies have facilitated logging, 
clearing for agriculture, subsistence farming, and road development. 
Habitat conversion and alteration are ongoing within Ecuador, including 
within protected areas.

Mexico

    This species is listed as endangered and is regulated under the 
general terms of the General Law of Ecological Balance and 
Environmental Protection (Ley General del Equilibrio Ecol[oacute]gico y 
Protecci[oacute]n al Ambiente (LGEEPA)), the General Wildlife Law (Ley 
General de Vida Silvestre (LGVS)), and also under CITES (CEC 2003, 
unpaginated). NOM-059-ECOL-2010 establishes a list of wildlife species 
classified as either in danger of extinction (endangered), threatened, 
under special protection, or probably extinct in the wild (Government 
of Mexico 2002, p. 6). All use of endangered and threatened species 
requires a special permit from the Secretariat of the Environment and 
Natural Resources (Secretar[iacute]a del Medio Ambiente y Recursos 
Naturales (SEMARNAT). SEMARNAT's main goal is to protect, restore, and 
conserve its ecosystems and natural resources. Under Mexico's General 
Wildlife Law, the use of these protected species, including the 
military macaw, may be authorized only when priority is given to the 
collection and capture for restoration, repopulation, and 
reintroduction activities (Comisi[oacute]n Nacional Para El 
Conocimiento y Uso de la Biodiversidad 2009, unpaginated; CEC 2003, 
unpaginated).
    International trade of Mexico's wildlife is also managed by 
SEMARNAT. In 2008, Mexico passed Article 60_2 to amend its General 
Wildlife Law. The article bans the capture, export, import, and 
reexport of any species of the Psittacidae (parrot) family whose 
natural distribution is within Mexico (Cant[uacute] and S[aacute]nchez 
2011, p. 1). It allows authorizations for the removal of individuals 
from the wild to be issued only for conservation purposes, or to 
accredited academic institutions for scientific research. However, it 
does not appear to be adequate based on investigations of trade of 
Mexico's native parrot species.
    The military macaw falls under the jurisdiction of several other 
laws in Mexico. The General Law on Sustainable Forest Management (Ley 
General de Desarrollo Forestal Sustenable (LGDFS 2003)) governs forest 
ecosystems in Mexico, including military macaw habitat. This law 
formalizes the incorporation of the forest sector in a broader 
environmental framework. Under this law, harvesting of forests requires 
authorization from SEMARNAT. It also requires that harvesting forests 
is based on a technical study and a forest management plan (GOM 2010, 
p. 24). A number of additional laws complement the 2003 law in 
regulating forest use. The LGEEPA regulates activities for protecting 
biodiversity and reducing the impact on forests and tropical areas of 
certain forest activities; the LGVS governs the use of plants and 
wildlife found in the forests; the General Law on Sustainable Rural 
Development (Ley General de Desarrollo Rural Sustentable) provides 
guidance for activities aimed at protecting and restoring forests 
within the framework of rural development programs; and the Agrarian 
Law (Ley Agraria) governs farmers' ability to use forest resources on 
their land (Anta 2004, in USAID 2011, unpaginated).
    Another law regulating portions of the military macaw's habitat is 
the National System of Protected Natural Areas (Sistema Nacional de 
[Aacute]reas Naturales Protegidas (SINANP)). These protected natural 
areas are created by presidential decree, and the activities in them 
are regulated under the LGEEPA, which requires that the protected 
natural areas receive special protection for conservation, restoration, 
and development activities (Comisi[oacute]n Nacional de [Aacute]reas 
Naturales Protegidas (CONANP) 2011, unpaginated). These natural areas 
are categorized as: Biosphere Reserves, National Parks, Natural 
Monuments, Areas of Natural Resource Protection, Areas of Protection of 
Flora and Fauna, and Sanctuaries (CONANP 2011, unpaginated).
    Conservation strategies in Mexico rely heavily on natural protected 
areas, and biosphere reserves comprise most of the designated protected 
area in the country (Figueroa and Sanchez 2008, pp. 3324,

[[Page 59996]]

3234). The military macaw occurs in or near at least four biosphere 
reserves. Although some areas where this species occurs have protected 
status, Figueroa and Sanchez (2008, entire) found that, for example, 
the Sierra Gorda Biosphere Reserve was ineffective (as opposed to 
effective or weakly effective). This study specifically evaluated the 
effectiveness of Mexico's protected areas for preventing land use and 
land cover change. It assessed the effectiveness of national protected 
areas (NPAs) by quantifying (1) the rate of change and (2) the total 
extent of change, between 1993 and 2002, as well as (3) the percentage, 
in 2002, of areas transformed by human use; transformed areas included 
agriculture, cultivated and induced pastures, human settlements, and 
forestry plantations. The rate of change of transformed areas inside 
each NPA was also compared with that estimated for an equivalent area 
surrounding the NPA. They selected 69 federal decreed NPAs (out of 160 
NPAs decreed in Mexico) that were 1,000 ha (2,471 ac) or larger, which 
is the minimum area for conserving ecosystems in Mexico (Figueroa and 
Sanchez 2008, p. 3,225; Ord[oacute][ntilde]ez and Fl[oacute]rez-Villela 
1995, p. 11). The study found that, overall, only approximately 54 
percent of protected areas, including 65 percent of biosphere reserves, 
were effective.

Peru

    In Peru, this species is listed as vulnerable under Supreme Decree 
No. 034-2004-AG (2004, p. 276,855), and its protections fall under the 
jurisdiction of the National Institute of Natural Resources (Instituto 
Nacional de Recursos Naturales, INRENA). This Decree prohibits hunting, 
take, transport, and trade of protected species, except as permitted by 
regulation. The military macaw is thought to occur in at least three 
areas with protected status in Peru. The Peruvian national protected 
area system includes several categories of habitat protection (refer to 
Factor A). National reserves, national forests, communal reserves, and 
hunting reserves are managed for the sustainable use of resources (IUCN 
1994, p. 2). The designations of national parks, sanctuaries, and 
protection forests are established by supreme decree that supersedes 
all other legal claim to the land and, thus, these areas tend to 
provide some form of habitat protection (Rodr[iacute]guez and Young 
2000, p. 330). However, limited information is available with respect 
to the status of this species in Peru. We do not know if the occurrence 
of the military macaw within protected areas in Peru actually protects 
the species or mitigates threats to the species, and to what extent 
these protections are effective.

Venezuela

    In Venezuela, the military macaw is thought to exist in two parks: 
El [Aacute]vila National Park and Henri Pittier National Park. Limited 
information about the status of this species is available in Venezuela. 
Henri Pittier National Park (107,800 ha; 266,380 ac) was declared the 
first national park in Venezuela in 1937. This park is the largest 
national park of the Cordillera de la Costa (Coastal Mountain Range) 
region. The principal threats to this park include: fire, human 
encroachment, solid waste buildup, pollution, hunting, and limited 
resources for effective park management (ParksWatch 2011g, 
unpaginated). In many cases, the intensity of threats has increased. 
Prior to 1994, a team of government representatives, NGOs, 
universities, and aviculturists in Venezuela had developed both an 
action plan for the conservation of parrots and a book containing 
information on parrot biology (Morales et al. 1994, in Snyder 2000, p. 
125). However, currently, it is unclear what conservation initiatives 
are occurring.
    El [Aacute]vila National Park (81,800 ha; 202,132 ac in size), is 
located along the central stretch of the Cordillera de la Costa 
Mountains in northern Venezuela. The most immediate threats to the park 
are forest fires and illegal settlements, which occur primarily near 
Caracas (ParksWatch 2011f, unpaginated). ParksWatch notes that the 
areas closest to the city have experienced more problems in the more 
isolated northern slope and eastern sector of El [Aacute]vila. Other 
threats in this park include the presence of nonnative plants and 
poaching.

Summary of Factor D

    In Argentina, Ecuador, Peru, and Venezuela, we recognize that 
conservation activities are occurring, and that these activities may 
have a positive effect on the species at the local population level. 
Parrots, in general, are long-lived with low reproductive rates, traits 
that make them particularly sensitive to poaching and other threats 
such as habitat loss (Lee 2010, p. 3; Thiollay 2005, p. 1,121; Wright 
et al. 2001, p. 711). The primary threats to this species historically 
have been the loss of habitat and capture for the pet trade (Strewe and 
Navarro 2003, p. 33). Since regulatory mechanisms such as CITES and the 
WBCA have been put into place, particularly since 1992, much of the 
legal international trade in the military macaw has declined (see 
Factor B discussion, above). However, those pressures prior to the 
military macaw's listing under CITES and the WBCA contributed 
significantly to the decline in population numbers for this species. 
Since then, the species' habitat has become fragmented, its range has 
reduced, and its populations have more difficulty finding suitable 
habitat.
    Each of these countries has enacted laws to protect its wildlife 
and habitat. The populations of this species in these four countries 
are likely to number from fewer than 100 to a few hundred individuals. 
There are numerous threats acting on this species; its populations have 
severely declined. In some cases, the actual causes of decline may not 
be readily apparent and a species may be affected by more than one 
threat in combination. Habitat conservation measures within these range 
countries do not appear to sufficiently mitigate future habitat losses. 
Habitat loss and degradation continue to occur within these countries; 
the best available information does not indicate that the existing 
regulatory mechanisms have mitigated these threats in the range of this 
species. Because these populations of this species are very small in 
these countries, any impact is likely to have a significant impact on 
the species; therefore, we are unable to conclude that regulatory 
mechanisms in place for this species and its habitat are adequate.
    Bolivia, Colombia, and Mexico have enacted various laws and 
regulatory mechanisms for the protection and management of this species 
and its habitat. Although information available is limited, the best 
evidence suggests that the military macaw exists in small populations 
in several large protected areas within these countries. As discussed 
under Factor A, the military macaw prefers primary forests and 
woodlands and complex habitat that offers a variety of food sources. 
Its suitable habitat has been severely constricted due to 
deforestation. In these three countries, there is evidence of threats 
to this species due to activities such as habitat destruction and 
degradation, poaching, construction of roads, and mining, as well as 
decreased viability due to small population sizes, despite the 
regulatory mechanisms in place. We acknowledge that research and 
conservation programs are occurring in these countries. However, based 
on the best available information, we find that the existing regulatory 
mechanisms for these countries are either inadequate or inadequately 
enforced in order to protect the species or to mitigate ongoing habitat 
loss and degradation, poaching, and the severe population decline of 
this species.

[[Page 59997]]

Habitat conservation measures within these range countries do not 
appear to sufficiently mitigate future habitat losses.
    Based on the best available information, we are unable to conclude 
that the existing regulatory mechanisms currently in place sufficiently 
mitigate threats to the military macaw throughout its range. Therefore, 
we find that the existing regulatory mechanisms are inadequate to 
mitigate the current threats to the continued existence of the military 
macaw throughout its range now and into the future.

E. Other Natural or Manmade Factors Affecting Its Continued Existence

Small Population Size

    Small, declining populations can be especially vulnerable to 
environmental disturbances such as habitat loss (O'Grady 2004, pp. 513-
514). Removal of a few birds from a population of 100 can have a 
greater effect than removal of a few birds from larger populations. In 
order for a population to sustain itself, there must be enough 
reproducing individuals and habitat to ensure its survival. 
Conservation biology defines this as the ``minimum viable population'' 
requirement (Grumbine 1990, pp. 127-128). This requirement may be 
between 500 and 5,000 individuals depending on variability, demographic 
constraints, and evolutionary history. The military macaw occurs in 
relatively small populations (ranging from a few pairs to approximately 
100 individuals, with the total population size that is likely no 
greater than a few thousand). The military macaw relies on specific 
habitat to provide for its breeding, feeding, and nesting. 
Historically, the military macaw existed in much higher numbers in more 
continuous, connected habitat. Its suitable habitat is becoming 
increasingly limited, and is not likely to expand in the future.
    The combined effects of habitat fragmentation and other factors on 
a species' population can have profound effects and can potentially 
reduce a species' respective effective population by orders of 
magnitude (Gilpin and Soul[eacute] 1986, p. 31). For example, an 
increase in habitat fragmentation can separate populations to the point 
where individuals can no longer disperse and breed among habitat 
patches, causing a shift in the demographic characteristics of a 
population and a reduction in genetic fitness (Gilpin and Soul[eacute] 
1986, p. 31). This is especially applicable for a species such as the 
military macaw that was once wide-ranging. It has lost a significant 
amount of its historical range due to habitat loss and degradation. 
Furthermore, as a species' status continues to decline, often as a 
result of deterministic forces such as habitat loss or overutilization, 
it will become increasingly vulnerable to other impacts. If this trend 
continues, its ultimate extinction due to one or more stochastic 
(random or unpredictable) events becomes more likely. The military 
macaw's current occupied and suitable range is highly reduced and 
severely fragmented. The species' small population size, its 
reproductive and life-history traits, and its highly restricted and 
severely fragmented range increase this species' vulnerability to other 
threats.

Climate Change

    Consideration of ongoing and projected climate change is a 
component of our analysis under the ESA. The term ``climate change'' 
refers to a change in the mean, variability, or seasonality of climate 
variables over time periods of decades or hundreds of years 
(Intergovernmental Panel on Climate Change (IPCC) 2007, p. 78). 
Forecasts of the rate and consequences of future climate change are 
based on the results of extensive modeling efforts conducted by 
scientists around the world (Solman 2011, p. 20; Laurance and Useche 
2009, p. 1,432; Nu[ntilde]ez et al. 2008, p. 1; Margeno 2008, p. 1; 
Meehl et al. 2007, p. 753). Climate change models, like all other 
scientific models, produce projections that have some uncertainty 
because of the assumptions used, the data available, and the specific 
model features. The science supporting climate model projections as 
well as models assessing their impacts on species and habitats will 
continue to be refined as more information becomes available. While 
projections from regional climate model simulations are informative, 
various methods to downscale projections to more localized areas in 
which the species lives are still imperfect and under development 
(Solman 2011, p. 20; Nu[ntilde]ez et al. 2008, p. 1; Marengo 2008, p. 
1). The best available information does not indicate that climate 
change is impacting this species such that it is a threat.

Summary of Factor E

    A species may be affected by more than one threat acting in 
combination. Impacts typically operate synergistically, particularly 
when populations of a species are decreasing. Initial effects of one 
threat factor can later exacerbate the effects of other threat factors 
(Gilpin and Soul[eacute] 1986, pp. 25-26). Further fragmentation of 
populations can decrease the fitness and reproductive potential of the 
species, which will exacerbate other threats. Within the preceding 
review of the five factors, we have identified multiple threats that 
may have interrelated impacts on this species. The most significant 
threats are habitat loss and poaching, particularly because the species 
has such a small and fragmented population, and it requires a large 
range and variety of food sources. Lack of a sufficient number of 
individuals in a local area or a decline in their individual or 
collective fitness may cause a decline in the population size, despite 
the presence of suitable habitat patches. For example, the species' 
behavior of not nesting in areas where depredation or disturbance is 
likely may mean that a nest site is ``abandoned'' before nesting is 
even attempted. Thus, the species' productivity may be reduced because 
of any of these threats, either singularly or in combination. These 
threats occur at a sufficient scale so that they are affecting the 
status of the species now and will in the future.
    In addition, the species' current range is highly restricted and 
severely fragmented. The species' small population size, its 
reproductive and life-history traits, and its highly restricted and 
severely fragmented range increase the species' vulnerability to 
adverse natural events and manmade activities that destroy individuals 
and their habitat. The susceptibility to extirpation of limited-range 
species can occur for a variety of reasons, such as when a species' 
remaining population is already too small or its distribution too 
fragmented such that it may no longer be demographically or genetically 
viable (Harris and Pimm 2004, pp. 1,612-1,613). Therefore, we find that 
the species' small population size, in combination with other threats 
identified above, is a threat to the continued existence of the 
military macaw throughout its range now and in the future.

Finding and Status Determination for the Military Macaw

    We find that this species is endangered based on the above 
evaluation, and we are listing this species as endangered due to the 
threats described above that continue to act on this species. Within 
the preceding review of the five factors, we identified multiple 
threats that may have interrelated impacts on the species. For example, 
the productivity of military macaws may be reduced because of the 
effects of poaching and habitat loss, which are expected to continue to 
act on the species in the future. In cases where populations are very 
small, species mate

[[Page 59998]]

for life, and birds produce small clutch sizes, these effects are 
exacerbated. The susceptibility to extirpation of species with small 
and declining populations can occur for a variety of reasons, such as 
when a species' remaining population is already too small or its 
distribution too fragmented such that it may no longer be 
demographically or genetically viable (Harris and Pimm 2004, pp. 1,612-
1,613). This species exists generally in very small and fragmented 
populations, usually in areas with some form of protected status in 
Mexico, Bolivia, Peru, and Colombia, and to a limited extent Ecuador, 
Venezuela, and Argentina. Its life-history traits (such as mating for 
life and small clutch size) make it particularly susceptible to 
extinction because its populations are so small. Based on our review of 
the best available scientific and commercial information pertaining to 
the five factors, we found that many of these threats are similar 
throughout the species' range.
    In four of the countries (Argentina, Ecuador, Peru, and Venezuela), 
the populations are extremely small, and very little information about 
the status of the species is available in many parts of its range. It 
is not necessarily easy to determine (nor is it necessarily 
determinable) which potential threat is the operational threat. 
However, we believe that these threats, either individually or in 
combination, are likely to occur at a sufficient geographical scale to 
significantly affect the status of the species. Additionally, although 
we do not have precise genetic information about populations throughout 
this species' range, it is likely that there is some genetic transfer 
between populations. We believe this based on its demonstrated ability 
to fly long distances in search of food sources (Chosset and Arias 
2010, p. 5). The most significant threat, habitat loss and degradation, 
is prevalent throughout this species' range. Its suitable habitat has 
severely contracted, and habitat loss is likely to continue into the 
future. We do not find that the factors affecting the species are 
likely to be sufficiently ameliorated in the foreseeable future. 
Therefore, we find that listing the military macaw is warranted 
throughout its range, and we propose to list the military macaw as 
endangered under the ESA.

Great Green Macaw

Taxonomy
    The great green macaw (Ara ambiguus or ambigua, Linnaeus, 1766; 
Bechstein, 1811) is in the parrot (Psittacidae) family. It is known by 
various common names such as lapa verde, Buffon's macaw, Guacamayo 
verde mayor, Guara verde, and Papagayo de Guayaquil. It occurs as two 
subspecies. The nominate subspecies, Ara a. ambiguus, occurs from 
Honduras to north-west Colombia. The subspecies A. a. guayaquilensis 
occurs in western Ecuador (Rodriguez-Mahecha et al. 2002, p. 116; 
Fj[euml]ldsa et al. 1987, pp. 28-31). There are believed to be only 
around 100 individuals of A. a. guayaquilensis in two areas in Ecuador. 
This subspecies has a smaller bill with greener underside of the flight 
and tail feathers than the nominate subspecies (Juniper and Parr 1998, 
p. 423). Avibase and ITIS both recognize these subspecies (http://www.itis.gov and http://avibase.bsc-eoc.org/avibase.jsp, accessed May 
5, 2014).
    There is no universally accepted definition of what constitutes a 
subspecies, and the use of the term subspecies varies among taxonomic 
groups (Haig and D'Elia 2010, p. 29). To be operationally useful, 
subspecies must be discernible from one another (i.e., diagnosable) and 
not merely exhibit mean differences (Patten and Unitt 2002, pp. 28, 
34). This element of discernibility is a common thread that runs 
through all subspecies concepts. Regarding the great green macaw, all 
populations or subspecies of Ara ambigua essentially face similar 
threats, all are generally in the same region (Central and northern 
South America), and all have small populations. In other words, they 
are not discernible between populations. For the purpose of this 
proposed rule and based on the best available information, we recognize 
all populations of great green macaws as a single species.
Description
    This species ranges between 77 and 90 cm (30 and 35 inches) in 
length and has a red frontal band above a large black bill, bare facial 
features with black lines, blue flight feathers on the superior 
feathers and olive inferior feathers, blue lower back, and orange tail 
(Juniper and Parr 1998, pp. 423-424). It is the second largest New 
World macaw. This species is not sexually dimorphic, meaning there are 
no differences in appearance between males and females of the same 
species. The great green macaw is very similar in appearance to the 
military macaw, but the military macaw has more prominent blue coloring 
on its hind neck, has darker plumage, and is smaller. These two species 
are also separated geographically.
Range, Observations, and Population Estimates
    The great green macaw is patchily distributed in a 100,000-km\2\ 
(38,610-mi\2\) area (BLI 2014b, p. 2). In addition to occupying humid 
tropical forests primarily in Central America (Costa Rica, Honduras, 
Nicaragua, and Panama), there are small remnant populations in western 
Ecuador, as well as northern Colombia (Berg et al. 2007, p. 1; Chassot 
et al. 2006, p. 7). Although there may be some interaction between 
populations, the great green macaw is fragmented into seven isolated 
populations throughout its distribution due to habitat loss (Monge et 
al. 2009, pp. 159, 174).
    Deforestation has reduced this species' habitat and concentrated 
its population into primarily five areas: the border of Honduras and 
Nicaragua, the border of Nicaragua and Costa Rica, the Dari[eacute]n 
region of Panama and Colombia, and two very small populations in 
Ecuador (Hardman 2011, p. 8; Monge et al. 2009, p. 159).
    Population estimates were made in the 1990s and early 2000s. In 
1993, the population estimate was 5,000 individuals; in 2000, the 
population was estimated to be between 2,500 and 10,000 birds (BirdLife 
International 2014b, p. 4; Rodr[iacute]guez-Mahecha 2002a). The global 
population is now likely less than 2,500 mature individuals (or less 
than 3,700 with juveniles included) (Monge et al. 2009, pp. 213, 256); 
however, the actual population is far from clear. Although historical 
observations are useful for assessing the range of the species, they 
may also be biased because surveys may not have sampled randomly. Thus, 
historical population estimates of this species may not be accurate. 
Although the population in Costa Rica is increasing, the population 
continues to be very small (Monge et al. 2010, p. 16), and researchers 
believe that the global population of this species is decreasing 
(Botero-Delgadillo and P[aacute]ez 2011, p. 91). Specific information 
about the range and population estimate for each country is discussed 
below.

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[GRAPHIC] [TIFF OMITTED] TR02OC15.011

Colombia

    Historically in Colombia, it was found in the north of the 
Serran[iacute]a de Baud[oacute],the West Andes, and east of the upper 
Sin[uacute] valley (Snyder et al. 2000, pp. 121-123). In the late 
1990s, this species was observed in Los Kat[iacute]os National Park, 
around Utr[iacute]a National Park in Serran[iacute]a de Baud[oacute] 
(Salaman in litt. 1997), and the Choc[oacute] area of western Colombia 
(Angehr in litt. 1996 in Snyder et al. 2000, pp. 121-123; Ridgley 
1982). This species' potential geographical range is 51,777 km\2\ 
(19,991 mi\2\), which includes two core areas in Sierra Nevada de Santa 
Marta and in the center of Antioquia Department of Columbia (Salaman et 
al. 2009, p. 21; Monge et al. 2009, unpaginated; Quevado-Gill et al. 
2006, p. 15). The total Columbian population is currently unclear but 
it is now believed to primarily exist in Los Kat[iacute]os National 
Park, which borders the Dari[eacute]n region in Panama. It was also 
recently observed in the area of Sabanalarga, Antioquia (Quevado-Gill 
et al. 2006, p. 15). Even though the largest population is thought to 
be in the northern Dari[eacute]n border region with about 1,700 adults, 
researchers believe this is an estimate without a strong basis (Botero-
Delgadillo and P[aacute]ez 2011, p. 91). The populations in Colombia 
are highly localized, and this number could be an overestimate (Botero-
Delgadillo and P[aacute]ez 2011, p. 91).

Costa Rica

    The great green macaw historically inhabited forests along the 
Caribbean lowlands of Costa Rica (Chosset et al. 2004, p. 32). The 
population has increased in that area since 1994, when there was an 
estimate of 210 birds. The population appears to have fluctuated; in 
2004, it was estimated that a maximum of 35 pairs were breeding in 
northern Costa Rica (Chosset et al. 2004, p. 32). A survey conducted in 
2009 reported a population estimate of 302 in Costa Rica (Monge et al. 
2009, p. 12); another estimate was that there was a total of 275 birds 
in Costa Rica in 2010 (Chassot 2010 pers. comm. in Hardman 2011, p. 
11).
    Approximately 67,000 ha (165,561 ac) of great green macaw breeding 
territory now remains in Costa Rica (Chun 2008, p. v), which is less 
than 10 percent of its original suitable habitat (Monge et al. 2010, p. 
15; Chosset et al. 2004, p. 38). Potential great green macaw breeding 
habitat, excluding Ecuador, is defined by the density of almendro 
trees, which this species uses for its primary feeding and nesting 
substrate. Almendro trees are found only on the Atlantic coast from 
southern Nicaragua down through Costa Rica and Panama and into 
Colombia, primarily at altitudes below 900 m (2,953 ft). Based on the 
assumption that great green macaw breeding pairs require 550 ha (1,359 
ac) of non-overlapping habitat, Chun postulated that northern Costa 
Rica could support about 120 breeding pairs (2008, p. 110). Chun notes 
that even the forested areas identified as individual ``patches'' 
through a geographic information system (GIS) program do not 
necessarily represent areas of forest with continuous canopy cover 
(indicating complex, fairly undisturbed habitat that is likely to 
contain nutritional needs for this species). Although these patches of 
forest are technically connected at some level, they are for the most 
part highly porous and discontinuous, and no analysis was performed to 
filter out stands that might be porous or discontinuous. There are some 
areas in its potential range that are above the elevation threshold for 
almendro trees, and do not meet the criteria for suitable habitat.

Ecuador

    In Ecuador, there may only be one viable population. This 
population exists in the Cerro Blanco Protected Forest, which is 6,070 
ha (15,000 ac) outside of Guayaquil in Guayas Province (Villate et al. 
2008, p. 19). This population is believed to be approximately 10 
individuals. An overall estimate of 60 to 90 individuals in Ecuador in 
2011 may be optimistic (Horstman pers. comm. in Hardman

[[Page 60000]]

2011, p. 12). Ecuador's population in 2002 was estimated to be between 
60 and 90 individuals (Monge et al. 2009, p. 256), but the population 
was reported to be rapidly decreasing. In addition, this is a decline 
from 1995, when the population was estimated to be approximately 100 
birds in Esmeraldas Province alone (Waugh 1995, p. 10). Between 1995 
and 1998, some individuals were observed in the Playa de Oro area along 
the Santiago River (Jahn 2001, pp. 41-43). In 2005, the species was 
described as being found in scattered forest remnants in coastal 
Ecuador from Guayas to Esmeraldas Province (Horstman 2005, p. 3).
    In addition to the small population in the Cerro Blanco Protected 
Forest, recently reported to be about 10 individuals, there may be 
another small group in the Rio Canande Reserve, which is a humid 
tropical forest and is located in the Esmeraldas province in coastal 
northern Ecuador (Horstman pers. comm. in Hardman 2011, p. 12). Rio 
Canande Reserve (1,813 ha or 4,478 ac) is one of eight reserves managed 
by another NGO, the Jocotoco Foundation. The most recent population 
census in Ecuador was conducted in the provinces of Esmeraldas, Santa 
Elena, and Guayas. Five individuals were recently observed in the 
Bosque Protector Chong[oacute]n Colonche; one macaw was observed at the 
Hacienda El Molino, near the Cerro Blanco Protected Forest; and two 
macaws were seen at Rio Canande (Horstman 2011, p. 16). The Cordillera 
(mountain range) de Chong[oacute]n-Colonche is on the central pacific 
coast of Ecuador, located in the provinces of Guayas and Manabi. Some 
individual great green macaws have also been observed at Hacienda 
Gonzalez 40 km (25 mi) northwest of Guayaquil; however, these 
individuals may be part of the same population found in Cerro Blanco. 
In summary, the majority of individuals are believed to be in 
Esmeraldas Province, and very small numbers remain in the 
Chong[oacute]n-Colonche mountain range, Guayas.

Honduras

    In 1983, the great green macaw was common in lowland rain forests 
in the Moskitia (Mosquitia) area and eastern Olancho (Marcus 1983, p. 
623). The region known as the Moskitia includes both eastern Honduras 
and northern Nicaragua. Historically, the species was reported to occur 
in the areas of Juticalpa and Catacamas in Olancho (Marcus 1983, p. 
623). The species was observed daily in the Pl[aacute]tano River area 
in flocks of more than 10 individuals and almost daily in the Patuca 
River area, usually in pairs (Barborak 1997 in Snyder et al. 2000, pp. 
121-123). In August 1992, macaws were recorded on the Patuca River at 
Pimienta upstream from Wampusirpe (Wiendenfeld in Monge et al. 2009, p. 
242). Currently, this species exists in the Rio Pl[aacute]tano 
Biosphere Reserve (800,000 ha or 1,976,843 ac), which has been 
described as one of the most important reserves in Central America 
(Anderson et al. 2004, p. 447).

Nicaragua

    In Nicaragua, the great green macaw is found primarily in lowland, 
tropical, and rain forest, as well as pine barrens, primarily in the 
Bosawas Reserve in the north and around the Indio-Ma[iacute]z and San 
Juan rivers in the south (Stocks et al. 2007, p. 1503; Martin[eacute]z-
S[aacute]nchez 2007; Chassot 2004, p. 36). The name Bosawas is derived 
from three significant geographic landmarks that delineate the 
reserve's core zone limits: The Bocay River, Mount Saslaya, and the 
Waspuk River. The Bosawas protected area contains habitat that is vital 
to the species. In the buffer zone of the Indio-Ma[iacute]z Biological 
Reserve, great green macaw nesting locations have been identified. The 
Indio-Ma[iacute]z Biological Reserve is located in Nicaragua just 
across the San Juan River at the northern border of Costa Rica, and is 
nearly 264,000 ha (652,358 ac) in size. The Nicaragua and Costa Rica 
macaw populations intermix; macaws have been observed crossing the San 
Juan River, which separates Nicaragua and Costa Rica. As of 2006, in 
the Quezada, Bijagua, Samaria, and La Juana communities, five macaw 
nests had been located during surveying. As of 2010, 35 active nests 
had been documented in the Indio-Ma[iacute]z Biological Reserve (Monge 
et al. 2010, p. 16).
    In 1999, Powell et al. estimated that the Nicaraguan great green 
macaw population could be 10 times the size of the population in Costa 
Rica. In 2008, a population viability analysis was conducted that 
indicated the size of the great green macaw population in Nicaragua was 
661 individuals (Monge et al. 2010, p. 21). In 2009, a population 
census was conducted, during which 432 macaws were observed. The 
researchers suggest that the ``average population'' in Nicaragua is 532 
(Monge et al. 2010, p. 13). This 2009 study yielded an estimated 
population of 834 individuals in Costa Rica and Nicaragua combined 
(Monge et al. 2010, p. 21).

Panama

    In Panama, the great green macaw is believed to inhabit the 
following areas: Bocas del Toro, La Amistad, northern Veraguas, Colon, 
San Blas, Dari[eacute]n, and Veraguas South (Monge et al. 2009, 
unpaginated). The species has been described as locally fairly common 
near Cana, Alturas de Nique, in 2005 (Angehr in litt. 2005). As of 
2009, the historical distribution in Panama was described as not well 
known due to lack of information (Monge et al. 2009, p. 68). The most 
viable population is believed to be in Dari[eacute]n National Park, 
Panama, which borders Colombia (Monge et al. 2009, p. 68; Angehr in 
litt. 1996 in Snyder et al. 2000, pp. 121-123; Ridgley 1982). 
Researchers believe the Dari[eacute]n area may contain the largest 
overall population of the great green macaw. However, there is little 
recent information to confirm this (Monge et al. 2009, p. 68). 
Dari[eacute]n National Park is the largest national park in Panama, and 
one of the largest tropical forest protected areas in Central America 
(The Nature Conservancy (TNC) 2011, p. 1). The Dari[eacute]n region 
encompasses nearly 809,371 ha (2 million acres) of protected areas, 
including Dari[eacute]n National Park and Biosphere Reserve, Punta 
Pati[ntilde]o Natural Reserve, Brage Biological Corridor, and two 
indigenous reserves (TNC 2011, p. 1). La Amistad, an area that may have 
a fairly viable population, connects suitable habitat in Panama such as 
Cerro Punta, Rio Pl[aacute]tano, and the Dari[eacute]n region, and 
connects the remote hills of Bocas del Toro Province with habitat in 
Costa Rica. La Amistad is approximately 200,000 ha (500,000 acres) in 
area.

Summary of Population Estimate

    The global population of great green macaws is estimated to be 
between 2,500 and 3,700 mature individuals (BLI 2014b, p. 4; Chassot 
and Arias 2012, p. 61; Monge et al. 2009, p. 213; Jahn in litt. 2005, 
2007, unpaginated). Based on the best available information from 
experts, the total population is likely between 1,000 and 3,000 
individuals (Botero-Delgadillo and P[aacute]ez 2011, p. 91; Monge et 
al. 2009, p. 213; Monge et al. 2009b, p. 68). In Ecuador, the 
population is estimated to be between 30-40 individuals (Horstman in 
litt in BLI 2014, p. 3). In 2009, a census was conducted in Costa Rica 
and Nicaragua (Monge et al. 2010, p. 13). A total of 173 individuals 
were observed in the Costa Rican study area, and 432 individuals were 
observed in the Nicaraguan study area during the breeding season (Monge 
et al. 2010, p. 22), with the areas of M[oacute]nico, Romerito, and 
Bartola having the highest estimated abundance at the time of each 
census. The population of the great green macaw for Costa Rica is 
currently estimated to be approximately 302 individuals, and the 
population for

[[Page 60001]]

Nicaragua is roughly estimated to be 834 individuals (Monge et al. 
2010, p. 22). Species with strict habitat requirements such as the 
great green macaw are particularly subject to population size 
overestimation, because they are unlikely to be present in suboptimal 
habitat despite those habitats being included as part of the species 
range (Jetz et al. 2008, p. 116-117). Thus, additional surveys are 
needed, and ground-truthing (gathering data regarding where the species 
is located) is essential to obtain accurate population estimates for 
this species.

Habitat and Life History

    The great green macaw inhabits humid lowland foothills and 
deciduous forests generally below 600 m (1,968 ft), but also may occur 
between 1,000 and 1,500 m (3,281 and 4,921 ft) depending on suitable 
habitat, which is primarily based on the presence of almendro (Dipteryx 
panamensis) trees. The type of habitat preferred by the great green 
macaw is an ecosystem where the almendro tree and Pentacletra macroloba 
(oil bean tree) dominate (Chassot et al. 2006, p. 35). This species' 
nests have been found in Carapa nicaraguensis (caobilla), Enterolobium 
schomburgkii (guanacaste blanco), Goethalsia meiantha, Prioria 
copaifera (cativo), and Vochysia ferruginea (botarrama) trees (Chosset 
and Arias 2010, p. 14; Powell et al. 1999). Nests have been observed in 
large trees, with cavities that are nearly 20 m (66 ft) above ground 
(Rodriguez-Mahecha 2002, p. 119). Great green macaws have been observed 
to use the same nesting cavity for many years if they are undisturbed, 
although they may alternate nest sites each year (Chun 2008, p. 102). 
Reproductive capability is generally reached between ages 5 and 6 years 
(Chassot et al. 2004, p. 34). The great green macaw mates for life, and 
nests in deep cavities (usually of almendro trees) from December to 
June (Chassot et al. in Villate et al. 2008, p. 19; Monge et al. 2002, 
p. 39). The incubation time is 26 days and the nesting period is 12 to 
13 weeks (Rodriguez-Mahecha et al. 2002, p. 119). After the breeding 
season, individuals disperse from the lowlands to higher forests in the 
mountains in search of food (Powell et al. 1999 in Chosset et al. 2004, 
p. 38).
    The great green macaw has been observed in flocks of up to 18 
individuals, and has been observed traveling long distances on the 
Caribbean slope. Macaws are strong fliers and are known to travel 
hundreds of kilometers (Chosset and Arias 2010, p. 5; Chosett et al. 
2004, p. 36). During a study in the late 1990s, macaws fitted with 
radio transmitters demonstrated that macaws migrate seasonally based on 
food availability, and were found to travel between 40 and 58 km (25 to 
36 mi) while in search of food (Chosset et al. 2004, p. 35).

Diet

    The great green macaw has been observed feeding on fruits of 37 
tree species (Berg et al. 2007, p. 2; Chassot et al. 2006, p. 35). 
While it is closely associated with the almendro tree, its diet varies 
based on location. In Ecuador, it was observed feeding on the following 
tree species: Cordia eriostigma (totumbo), Cynometra sp. (cocobolo), 
Ficus trigunata (matapalo), Ficus sp. (higuer[oacute]n), Psidium 
acutangulum (Guayaba de monte), Chrysophyllum caimito (caimito), and 
Vitex gigantea (tillo blanco or pechiche) (Berg et al. 2007, p. 2; 
Waugh 1995, p. 7). In other parts of its range, it has also been 
observed feeding on Cavanillesia platanifolia (NCN), Cecropia litoralis 
(pumpwood or trumpet tree), Centrolobium ochroxylum (amarillo de 
guayaquil), Cochlospermum vitifolium (buttercup tree), Lecythis ampla 
(sapucaia), Leucaena trichodes (NCN), Odroma pyramidalis (NCN), 
Pseudobombax guayasen (NCN), Pseudobombax millei (beldaco), Rafia 
species (believed to be palms), Sloanea spp., Symphonia globulifera 
(NCN), and Terminalia valverdeae (guarapo) (Berg et al. 2007, p. 6). 
One preferred plant species, Cynometra bauhiniifolia (NCN), produced 
more food than nine other species (Berg et al. 2007, p. 1). In another 
study, two of the most important sources of food for the great green 
macaw, in addition to the almendro tree, were found to be Sacoglottis 
trichogyna (titor, rosita, or manteco) and Vochysia ferruginea (NCN) 
(Herrero-Fernandez 2006, p. 9; Chassot et al. 2006, p. 35). S. 
trichogyna fruits were observed to be its preferred food when D. 
panamensis was scarce or unavailable in Costa Rica (Chassot et al. 
2004, p. 34).

Almendro Trees

    The great green macaw is closely associated with almendro trees 
(Dipteryx panamensis) for feeding and nesting in the majority of its 
range (Chun 2008, p. iv; Chosset et al. 2004, p. 34). Because the great 
green macaw is highly dependent on the almendro tree, we are describing 
almendro tree habitat, its life history, and factors that affect its 
habitat. The almendro tree (also known as the tropical almond or 
mountain almond tree) is a member of the pea family (Fabaceae; 
Papilionoideae) and bears compact, single-seeded drupes. The seeds are 
encased in a thick woody endocarp that has been observed to persist on 
the forest floor for up to 2 years (Hanson 2006, p. 68). This tree 
species is only located in southern Nicaragua, Costa Rica, Panama, and 
Colombia, where it grows primarily in the lowlands of the Atlantic 
plains. They require an annual rainfall of 3 to 5 m (approximately 10 
to 16 ft) (Schmidt 2009, p. 14) for optimal growth. A 2008 study 
reported that nearly 90 percent of all great green macaw nests 
identified in northern Costa Rica are located within hollowed cavities 
of large almendro trees (Chun 2008, p. 109). Additionally, almendro 
trees were found to provide 80 to 90 percent of both the macaw's food 
and nesting needs. Great green macaw pairs tend to select nesting trees 
that are surrounded by relatively dense stands of reproducing almendro 
trees (Chun 2008). Almendro tree fruit sustains the adults, chicks, 
nestlings, and fledglings over the course of the breeding and 
development season, which coincides with the peak production of 
almendro fruit (November through March).
    Likely pollinators of the almendro tree are bees within the genera 
Bombus, Centris, Melipona, Trigona, and Epicharis (Thiele 2002 in 
Hanson 2006, p. 3; Flores 1992, pp. 1-22; Perry et al. 1980, p. 310). 
These trees are referred to as ``emergent'' because they are the 
tallest trees in the forest. Almendro trees can grow to over 46 m (150 
ft) and reach a diameter of 1.5 m (4.92 ft). Three hundred-year-old 
trees have been documented, but research suggests that the almendro 
tree has a maximum potential age of 654 years (Fichtler et al. 2003 in 
Schmidt 2009, p. 15).
    Wood from the almendro tree is heavy, commercially valuable, and 
yields the highest prices on local markets (Rodriguez and Chaves 2008, 
p. 5). It is used for furniture, floorings, bridges, railroad ties, 
boats, marine construction, handicrafts, veneers, industrial machinery, 
sporting equipment, springboards, and agricultural tool handles 
(Schmidt 2009, p. 16). Almendro outsells every other tree species on 
the Costa Rican timber market (Grethel and Norman 2009 in Schmidt 2009, 
p. 77; Rodriguez and Chaves 2008, p. 5). It was listed in Appendix III 
of CITES by Costa Rica in 2003 and by Nicaragua in 2007 (http://www.cites.org). A species is unilaterally listed in Appendix III by a 
country in the native range of that species, at the request of that 
country. Article II, paragraph 3, of CITES states that ``Appendix III 
shall include all species which any Party identifies as being

[[Page 60002]]

subject to regulation within its jurisdiction for the purpose of 
preventing or restricting exploitation, and as needing the cooperation 
of other parties in the control of trade.'' For the export of specimens 
of an Appendix-III species from a country that has listed the species, 
the Management Authority in that country of export needs to determine 
that the specimens were not obtained in contravention of that country's 
laws. In addition to CITES protections, a recent decision by the fourth 
Chamber of Costa Rica's Supreme Court in 2008 required the Ministry of 
Environment and Energy (MINAE, or Ministerio de Ambiente y Energia) to 
abstain from the use, exploitation, or extraction of almendro trees 
(Chun 2008, p. 113).
    Recent research found that this tree species is much more 
restricted to lowland habitat than previously described; it is 
predicted to occur between 45 and 125 m (147 to 410 ft) in elevation, 
in part based on its soil requirements (Schmidt 2009, p. iv; Chun 2008, 
p. 109). The almendro tree is best adapted to areas with high levels of 
rainfall and acidic clay soils with good drainage below elevations of 
500 m (1,640 ft) such as the Atlantic lowlands of Costa Rica (Schmidt 
2009, p. iv). Almendro trees require at least 2,000 millimeters (mm) 
(79 inches) of rainfall per year for optimal growth (Schmidt 2009, p. 
69).
    Great green macaw breeding pairs are believed to require a home 
range of 550 ha (1,359 ac) (Chun 2008, p. 105). Because the great green 
macaw requires such a large range, and is strongly associated with 
almendro trees, range countries such as Nicaragua and Costa Rica have 
developed conservation plans for the almendro tree. Almendro trees 
commonly occur at a density of less than one adult tree per hectare 
(Hanson et al. 2008 in Schmidt 2009, p. 14; Hanson et al. 2006, p. 49). 
The highest density recorded was 4 trees per hectare (Chaverri and 
L[oacute]pez 1998). In one area of Costa Rica that was surveyed for 
almendro trees, of 140,178 ha (56,728 ac) surveyed, 20 percent 
exhibited densities of 0.50 almendro trees per hectare or more, and 50 
percent had densities of 0.20 trees per ha or more (Chun 2008, p. 103).
    Due to their important role in the ecosystem, particularly with 
respect to the great green macaw, conservation efforts have focused on 
the almendro tree. These trees not only provide habitat to many 
wildlife species such as the great green macaw, but they also play a 
significant role in the ecosystem. One conservation strategy for the 
great green macaw is to protect 30,159 ha (74,493 acres) of primary, 
secondary, and mangrove forest that remains in this species' nesting 
habitat. Another conservation strategy has been to establish almendro 
tree plantations. Due to its open crown structure, almendro has a 
relatively translucent canopy that produces only moderate shade, which 
allows for the production of shade canopy crops such as pineapple and 
cacao (Schmidt 2009, p. 19). These almendro plantations are being 
researched for several reasons, particularly due to the almendro tree's 
ability to resist decay, its ability to capture carbon dioxide, and its 
role in the ecosystem (Schmidt 2009, p. 11). Additionally, almendro 
trees have been identified as the most promising species for long-term 
carbon sink reforestation projects in Costa Rica (Redondo-Brenes 2007, 
p. 253; Redondo-Brenes and Montagnini 2006, p. 168).
    In Ecuador, the great green macaw is not dependant on almendro 
trees, although it still inhabits humid lowland areas (Juniper and Parr 
1998, p. 424). In this habitat, the great green macaw prefers Lecythis 
ampla (salero) in the Esmeraldas rainforest, Cynometra bauhiniaefolia 
(cocobolo) as a primary food source, and pigio (Cavanillesia 
platanifolia) as a nest tree (Chassot et al 2007, p. 1; Berg et al 
2007, pp. 1-3).

Conservation Status

    There are various protections in place for the great green macaw at 
the international, national, and local levels. At the international 
level, this species is listed as endangered on the IUCN Red List due to 
continuous loss of habitat, hunting, and poaching of this species for 
the pet trade (BLI 2013). IUCN's Red List classifies species as 
endangered (extinction probability of 20 percent within 20 years) or 
critically endangered (extinction probability of 50 percent within 10 
years) based on several criteria, including limited or declining ranges 
or populations. However, the status under IUCN conveys no actual 
protections. This species is listed in Appendix I of CITES. Appendix I 
includes species threatened with extinction that are or may be affected 
by international trade, and are generally prohibited from commercial 
trade. Refer to the discussion above for the military macaw for 
additional information about CITES. The great green macaw's 
conservation status in each country is discussed below and in more 
detail under Factor D.

Colombia

    The great green macaw is listed as Vulnerable on Colombia's Red 
List (Renjifo et al. 2002, p. 524). It has protected status in Los 
Kat[iacute]os National Park, Utr[iacute]a National Park, Paramillo 
National Park, and Farallones de Cali National Natural Park (Rodriguez 
et al. 2002, pp. 120-121). The largest population of the great green 
macaw is believed to exist in the Dari[eacute]n Endemic Bird Area (EBA) 
023, which encompasses southern Panam[aacute] and northwestern 
Colombia. However, there are no reliable population estimates for this 
area (Botero-Delgadillo and P[aacute]ez 2011, p. 91; Jahn in litt. 
2004). Colombia developed a National Action Plan for the Conservation 
of Threatened Parrots (Plan Nacional de Acci[oacute]n para la 
Conservaci[oacute]n de los Loros Amenazados), which was in effect until 
2007. The ProAves Foundation, an NGO in Colombia, has been active in 
parrot conservation since 2005. Other than NGO involvement, it is 
unclear what proactive, effective protections are in place for this 
species.

Costa Rica

    The great green macaw is considered to be endangered in Costa Rica 
(Monge et al. 2010, p. 22; Herrero 2006, p. 6; Executive Order No. 
26435-MINAE). Several intense conservation initiatives are underway for 
this species in Costa Rica. In 2001, a committee was formed to 
investigate a corridor for the conservation of this species' habitat. 
As a result, the San Juan-La Selva Biological Corridor was formed to 
connect the Indio Ma[iacute]z Biological Reserve in southeastern 
Nicaragua with the Central Volcanic Cordillera Range in Costa Rica. 
This links Costa Rica's La Selva Biological Station in the north to the 
Barra del Colorado Wildlife Reserve and National Park and Protective 
Zone of Tortuguero on Costa Rica's Caribbean coast. In addition, the 
conservation team lobbied for the establishment of the Maquenque 
National Wildlife Refuge to protect the macaw's breeding habitat 
(Hardman 2011, p. 10; Chun 2008, p. 98). This corridor makes up a part 
of the larger MesoAmerican Biological Corridor, which has been proposed 
to connect protected habitat from the Yucatan Region in southern Mexico 
and Belize to the Dari[eacute]n National Park in Panama (http://www.greatgreenmacaw.org/BiologicalCorridor.htm, accessed October 25, 
2011).
    The San Juan-La Selva binational corridor links existing protected 
wild areas. There is also an extended part to the northwest that 
includes the El Castillo area. The goal of this initiative is to 
provide linkages to 29 protected areas involving 1,311,182 ha 
(3,240,001 ac) (Chassot et al. 2006, p. 85). Because macaws are known 
to move hundreds of

[[Page 60003]]

kilometers (Chosset and Arias 2010, p. 5), these linkages should allow 
this species better access to different habitats so that it is able to 
meet its nutritional and nesting requirements. In addition to 
containing key conservation sites for the great green macaw, the 
corridor connects the vast expanse that includes Punta Gorda Natural 
Reserve, Cerro Silva Natural Reserve, and Fortaleza Inmaculada 
Concepci[oacute]n de Mar[iacute]a Historic Monument (Chassot et al. 
2006, p. 85). The corridor also provides connections among unprotected 
forest patches in Costa Rica in addition to providing connections to 
protected areas. Many of these areas may not be pristine habitat; some 
areas are either inhabited by humans or used by local communities to 
extract resources. However, there are conservation awareness programs 
in place throughout the corridor, and the great green macaw is being 
intensely managed and monitored in the San Juan-La Selva Biological 
Corridor.

Ecuador

    This species is categorized as critically endangered in Ecuador 
(Monge et al. 2009, p. 256), primarily due to deforestation and hunting 
pressures. In Ecuador, the only potentially population is believed to 
exist in the Cerro Blanco Protected Forest, which is 6,070 ha (15,000 
ac) in size. The Guayaquil subspecies of the great green macaw (Ara a. 
guyaquilensis) is thought to be in imminent danger of extinction (Berg 
2007, p. 1). In 2008, the National Preservation Strategy for the Great 
Green Macaw in Ecuador was described at the Great Green Macaw 
Population Viability Assessment and Habitat Conservation Workshop held 
in Costa Rica; however, funding is still lacking for many of the 
initiatives in Ecuador that have been prescribed as necessary for the 
conservation of this species.

Honduras

    The great green macaw is categorized as endangered in Honduras 
(List of Wildlife Species of Special Concern, Resolution No. Gg-003-98 
APVS). In 1990, the Government of Honduras prohibited the capture and 
sale of wildlife, including the great green macaw in Honduras. 
Currently, this species exists in the Rio Pl[aacute]tano Biosphere 
Reserve (which consists of 800,000 ha or 1,976,843 ac). The official 
designation of the Biosphere as a reserve is to protect and conserve 
biodiversity; however, this designation has not halted deforestation 
within the protected area (UNESCO 2011, p. 1; ParksWatch 2011; Wade 
2007, p. 65). Additionally, as of 2009, there were 23 areas in Honduras 
identified as Important Bird Areas (IBAs) (Devenish et al. 2009, p. 1) 
that may provide additional protections to this species in part by 
serving as ecotourism sites that can increase conservation efforts in 
the areas. For additional information on IBAs, see the discussion above 
for the military macaw.

Nicaragua

    Nicaragua follows the IUCN categorization of endangered for this 
species (Castellon 2008, pp. 13, 19; Lezama-L[oacute]pez 2006, p. 90). 
The great green macaw exists in the Indio-Ma[iacute]z Biological 
Reserve, which has had protected status since 1990, although threats to 
the species still exist in this Reserve (Herrera 2004, pp. 5-6). 
Nicaragua is also participating in the bi-national conservation 
strategy for this species (Monge et al. 2009, pp. 11, 16).

Panama

    There is little information available regarding the status of this 
species in Panama (Monge et al. 2009, p. 67); however, Panama follows 
the IUCN categorization for this species (Devenish et al. 2009, p. 
294). The great green macaw is believed to be in Dari[eacute]n National 
Park (Monge et al. 2009, p. 68). Panama's wildlife law of 1995, Law No. 
24, establishes the standards for wildlife conservation.

NGO Involvement

    There are many nongovernmental organization (NGO), private, and 
government efforts to protect this species, although not all of the 
projects and NGOs are identified in this document. NGOs have conducted 
collaborative efforts, such as training workshops, that are community-
focused and aimed at the conservation of the habitat. In Nicaragua, 
Fundaci[oacute]n Cocibolca is active in this species' conservation. 
This NGO first signed an agreement with Nicaragua's Natural Resources 
Ministry (MARENA) in 1996, at which time the conservation group was the 
first NGO to have been granted responsibility to manage a national 
protected area in Nicaragua (http://www.marena.gob.ni; accessed 
November 9, 2011; http://www.planeta.com, accessed November 9, 2011). 
The Nicaraguan conservation organization, Fundaci[oacute]n del Rio, 
works in the buffer zone of the Indio-Ma[iacute]z Biological Reserve, 
which borders the San Juan River (Villate 2008, p. 39). In 1999, 
Fundaci[oacute]n del Rio began an environmental education program in 
this buffer zone to promote awareness of the great green macaw and its 
habitat. In another area, as a result of conservation efforts, the 
local government of El Castillo declared this species the official 
municipal bird, and the city established sanctions to those intending 
to harm this species (Chassot et al. 2008, p. 23).
    Since 2001, Fundaci[oacute]n del R[iacute]o and the Tropical 
Science Center in Costa Rica have coordinated a binational campaign 
focused on promoting the awareness of the ecology of the great green 
macaw in the lowlands of the San Juan River area (Chassot et al. 2009, 
p. 9). Between 2002 and 2005, at least 11 workshops on great green 
macaw biology and preservation were held within communities of the 
buffer zone of Indio-Maiz Biological Reserve in Costa Rica (Chassot et 
al. 2006, p. 86). Some examples of projects initiated by NGOs include 
installation of nest boxes to increase nest availability and community 
heritage festivals that are focused on the great green macaw. Some NGOs 
are providing training to local communities to monitor populations, and 
some researchers are studying this species via satellite transmitters 
to determine the species' home range and specific habitat used (Chosset 
et al. 2004, p. 35). In Costa Rica and Nicaragua, 20 communities are 
participating in monitoring and protection activities of the great 
green macaw (Chosset and Arias 2010, p. 3). The primary objectives of 
the campaign have been to improve awareness by conducting workshops on 
the importance, threats, and conservation of the great green macaw and 
its habitat; to strengthen natural resources management by 
environmental authorities of both Nicaragua and Costa Rica, focusing on 
the local and international biological corridors; and to organize joint 
activities (Chassot et al. 2006, p. 83).
    In Colombia, the NGO ProAves has made great progress in forming 
partnerships at the local, regional, and international levels to carry 
out bird conservation initiatives (Chassot et al. 2008, p. 23; Quevado-
Gill et al. 2006, p. 18). Additionally, reforestation efforts have 
occurred (Monge et al. 2009, p. 263). These efforts have focused 
primarily within the reserves of the Colombian Civil Society 
Association Network (Quevado-Gill et al. 2006, p. 17). Conservation 
efforts and these workshops have been important because they have 
trained the community in sustainable development by linking local 
agricultural activities to the protection of natural resources 
(Quevado-Gill et al. 2006, p. 17).
    Three NGOs are active in the conservation of this species in 
Ecuador: Pro-Forest Foundation in Guayas

[[Page 60004]]

Province, Fundaci[oacute]n Natura, and the Jocotoco Foundation at the 
Rio Canande Reserve in Esmeraldas Province. The Pro-Forest Foundation 
(Fundaci[oacute]n ProBosque) was created in 1992, through a decree of 
the Ecuadorian Ministry of Agriculture. Its mission is to protect areas 
with an emphasis in reforestation, agroforestry, investigation, 
environmental education, and ecotourism programs, all in order to 
support the conservation of biodiversity.
    In Panama, the Asociaci[oacute]n Nacional para la 
Conservaci[oacute]n de la Naturaleza (ANCON) began conservation work in 
1991. The project has jointly worked on conservation efforts with 
Panama's Instituto Nacional de Recursos Naturales Renovables 
(INRENARE). ANCON has worked on training park rangers, marking and 
patrolling paths and park boundaries, acquiring property around parks 
and tree nurseries, and improving agricultural techniques (TNC 2011, p. 
2).
    Additionally, members from several NGOs participated in the great 
green macaw conservation workshop held in 2008. The purpose of the 
workshop was to bring together experts, to determine the priorities for 
the conservation of the species, and to develop a plan for its 
conservation (Monge et al. 2009, entire). We acknowledge the 
substantial effort under way by various NGOs in the range countries of 
this species to protect it and its habitat. Despite many efforts in 
place, the populations of the great green macaw continue to face many 
threats to its habitat.

Evaluation of Threat Factors

Introduction

    Section 4 of the ESA (16 U.S.C. 1533) and implementing regulations 
(50 CFR 424) set forth procedures for adding species to, removing 
species from, or reclassifying species on the Federal List of 
Endangered and Threatened Wildlife and Plants. Under section 4(a)(1) of 
the ESA, a species may be determined to be endangered or threatened 
based on any of the following five factors:
    A. The present or threatened destruction, modification, or 
curtailment of its habitat or range;
    B. Overutilization for commercial, recreational, scientific, or 
educational purposes;
    C. Disease or predation;
    D. The inadequacy of existing regulatory mechanisms; and
    E. Other natural or manmade factors affecting its continued 
existence.
    In making this finding, information pertaining to the great green 
macaw in relation to the five factors in section 4(a)(1) of the ESA is 
discussed below. In considering what factors might constitute threats 
to a species, we must look beyond the exposure of the species to a 
particular factor to evaluate whether the species may respond to that 
factor in a way that causes actual impacts to the species. If there is 
exposure to a factor and the species responds negatively, the factor 
may be a threat, and, during the status review, we attempt to determine 
how significant a threat it is. The identification of factors that 
could impact a species negatively may not be sufficient to compel a 
finding that the species warrants listing. The information must include 
evidence sufficient to suggest that these factors, singly or in 
combination, are operative threats that act on the species to the point 
that the species may meet the definition of endangered or threatened 
under the ESA.
    This rule focuses primarily on where this species has been 
documented, which is generally in parks and other areas with protected 
status and the peripheral zones. In some cases, we will evaluate the 
factor by country. In other cases, we may evaluate the factor by a 
broader region or context, for example, if we do not have adequate 
information specific to a particular country about this species. This 
is because often threats are the same or very similar throughout the 
species' range.

A. The Present or Threatened Destruction, Modification, or Curtailment 
of Its Habitat or Range

    Throughout the range of this species, the factors impacting the 
great green macaw are generally very similar. The main factors 
affecting this species are habitat loss and degradation, and poaching 
(McGinley et al. 2009, p. 11; Berg et al. 2007; Chassot et al. 2006; 
Quevado-Gill et al. 2006, p. 16; Guedes 2004, p. 280). Both Central and 
South America continue to experience high levels of deforestation (FAO 
2010, p. xvi). Habitat loss is primarily due to conversion of the 
species' habitat (generally forests) to agriculture and other forms 
that are not optimal for this species (Chosset and Arias 2010, p. 3; 
Monge et al. 2009, entire).
    Almendro habitat, this species' primary food and nesting source, 
has declined significantly (Schmidt 2009, p. 16), particularly since 
the 1980s. Almendro and other tree species used by the great green 
macaw have been selectively cut down and removed from this species' 
habitat. Selective logging is the practice of removing one or two 
generally large, mature trees and leaving the rest. Throughout the 
range of the great green macaw, its habitat has declined primarily due 
to competition for resources and human encroachment (Guedes 2004, p. 
279; Rodr[iacute]guez-Mahecha and Hern[aacute]ndez-Camacho 2002; 
Chassot and Monge 2002 in Rothman 2008, p. 509). Its habitat has 
continuously been clear-cut and converted to agriculture or human 
establishments, which is discussed in more detail below.
 Logging
    Tree species used by macaws tend to be large, mature trees with 
large nesting cavities. The practice of selective logging often targets 
old, large trees that macaws depend upon for nesting. In selective 
logging, the most valuable trees from a forest are commercially 
extracted (Asner et al. 2005, p. 480; Johns 1988, p. 31), and the 
forest is left to regenerate naturally or with some management until 
being subsequently logged again. Johns (1988, p. 31), looking at a West 
Malaysian dipterocarp forest, found that mechanized selective logging 
in tropical rainforests, which usually removes a small percentage of 
timber trees, causes severe incidental damage. He found that the 
extraction of 3.3 percent of trees destroyed 50.9 percent of the 
forest. Selective logging can cause widespread collateral damage to 
remaining trees, subcanopy vegetation, and soil, and the practice 
impacts hydrological processes, erosion, fire, carbon storage, and 
plant and animal species (Chomitz et al. 2007, pp. 117, 119; Asner et 
al. 2005, p. 480). Forests that were selectively logged 15 years prior 
became an open forest with skeletons of incidentally killed trees, 
serious gulley erosion, and vegetation on waterlogged sites that had 
been compacted by heavy vehicles (Edwards 1993, p. 9). Additionally, 
the availability of food sources for frugivores (fruit-eaters, such as 
the great green macaw) is reduced because the trees that contain 
nutritional sources are no longer there.
    Selective logging is particularly devastating to the almendro tree, 
which is slow growing and may take centuries to reach sufficient size 
to harbor cavities (Schmidt 2009, p. 15), and which great green macaws 
need for both food and shelter. The almendro tree's wood is of great 
commercial value due to its strength and durability for flooring, 
roofing, and irrigation systems (Madriz-Vargas 2004, p. 8). Concern for 
this tree species was significant enough that the species was listed as 
CITES Appendix III by both Costa Rica and Nicaragua. Listing species in 
Appendix III enhances conservation measures enacted for the species by 
regulating international trade in the species. In general, shipments 
containing CITES-

[[Page 60005]]

listed species receive greater scrutiny from border officials in both 
the exporting and importing countries. The elimination of almendro 
trees is possibly the most severe threat for the species in its range 
countries with the exception of Ecuador, where the decrease in 
availability of other tree species used by the great green macaw is a 
concern.
    Although the nest cavities that the macaws prefer (deep and dry) 
may take 10 to 20 years to form, the nests themselves can last for 
several decades (Chun 2008, p. 101). Even in undisturbed forests, 
suitable tree cavities are usually limited. As a result, each loss of a 
nest site can represent the loss of potentially many future chicks that 
could have been raised in each tree cavity.
Agriculture
    Habitat degradation, particularly due to conversion of forest 
habitat to agriculture or plantations, is a major factor affecting 
great green macaws. The clearing of forests and buffer zones for the 
development of plantations for bananas, oil palms, cacao, coffee, 
soybeans, and rice destroys great green macaw nesting sites and exposes 
chicks to poaching for the pet trade (Botero et al. 2011, p. 92; Monge 
et al. 2009, pp. 26, 29, 43, 54; Waugh 1995, p. 2). By 2005, the 
world's tropical forest biomes had decreased to less than 50 percent 
tree cover (Donald et al. 2010, p. 26), in part due to the above 
activities. Tropical forest fragmentation due to these activities 
continues to be a concern. A discussion of habitat loss and degradation 
for each country follows.

Colombia

    Very little information is available about the great green macaw's 
status in Colombia (Botero-Delgadillo and P[aacute]ez 2011, pp. 86, 90; 
Monge et al. 2009; Jahn in litt. 2004). A large population is believed 
to exist in Los Kat[iacute]os National Park, which borders the swampy 
and sparsely populated Dari[eacute]n region in Panama; however, there 
are no recent reported observations of the species in this area. 
Population surveys need to be conducted (Botero-Delgadillo et al. 2011, 
pp. 88, 90; Monge et al. 2009). At least 40 percent of the great green 
macaw's original distribution area in northwestern Colombia was 
deforested by 1997 (Etter 1998 in Jahn in litt. 2004). Threats to this 
species in Colombia have been identified as: Agriculture (particularly 
illegal coca cultivation), agroindustrial farms, large forest plantings 
of exotic trees, wood extraction, development of infrastructure, and 
hunting, capturing, and harvesting of this species (Botero-Delgadillo 
and P[aacute]ez 2011, pp. 91-92). Threats specific to Los Kat[iacute]os 
National Park are illegal deforestation and hunting (UNEP-WCMC 2009, p. 
1). In 2009, the threats in this park were so severe that the park was 
added to UNESCO's List of World Heritage Sites in Danger (http://whc.unesco.org/en/list/711, accessed January 17, 2012).
Deforestation
    Colombia has experienced extensive deforestation in the last half 
of the 20th century as a result of habitat conversion for human 
settlements, road building, agriculture, and timber extraction (FAO 
2010, p. 233; Armenteras et al. 2006, p. 354). A 23-year study, 
conducted from 1973 to 1996, found that these activities reduced the 
amount of primary forest cover in Colombia by approximately 3,605 ha 
(8,908 ac) annually, representing a nearly one-third total loss of 
primary forest habitat (Vi[ntilde]a et al. 2004, pp. 123-124). More 
than 70 percent of rural land of Colombia located in former forestlands 
is now devoted to cattle grazing (Etter and McAlpine 2007, pp. 89-92). 
Beginning in the 1980s, habitat loss increased dramatically as a result 
of influxes of people settling in formerly pristine areas (Perz et al. 
2005, pp. 26-28; Vi[ntilde]a et al. 2004, p. 124). More recent studies 
indicate that the rate of habitat destruction is accelerating (FAO 
2010, p. xvi). Between the years 1990 and 2005, Colombia lost 
approximately 52,800 ha (130,471 ac) of primary forest annually (Butler 
2006a, pp. 1-3).
    Primary forest habitats such as those used by the great green macaw 
throughout Colombia have undergone extensive deforestation. Vi[ntilde]a 
et al. (2004, pp. 123-124) used satellite imagery to analyze 
deforestation rates and patterns along the Colombian-Ecuadorian border 
(in the Departments of Putumayo and Sucumbios, respectively) and found 
that between 1973 and 1996, a total of 829 km\2\ (320 mi\2\) of 
tropical forests within the study area were converted to other uses. 
This corresponds to a nearly one-third total loss of primary forest 
habitat, or a nearly 2 percent mean annual rate of deforestation within 
the study area. Habitat loss and degradation, including conversion of 
this species' habitat to other forms of use such as agriculture, 
plantations, or harvesting of this species' plant food sources, 
continue to occur and affect the quality of this species' habitat.
    In addition to the direct detrimental effect of habitat loss, there 
are several indirect effects of habitat disturbance and fragmentation, 
such as road building (Brooks and Strahl 2000, p. 10). Roads increase 
human access into habitat, facilitating further exploitation, erosion, 
and habitat destruction (Chomitz et al. 2007, p. 88; Hunter 1996, pp. 
158-159). Research has documented that road building and other 
infrastructure developments in areas that were previously remote 
forested areas have increased accessibility and facilitated further 
habitat destruction and human settlement (Etter et al. 2006, p. 1; 
[Aacute]lvarez 2005, p. 2,042; C[aacute]rdenas and Rodr[iacute]guez-
Becerra 2004, pp. 125-130; Vi[ntilde]a et al. 2004, pp. 118-119; Hunter 
1996, pp. 158-159). A study conducted on the effects of habitat 
fragmentation on Andean birds within western Colombia determined that 
31 percent of the historical bird populations in western Colombia had 
become extinct or locally extirpated by 1990, primarily as a result of 
habitat fragmentation from deforestation and human encroachment (Kattan 
and [Aacute]lvarez-Lopez 1996, p. 5; Kattan et al. 1994, p. 141). 
Greater exposure of soil to direct sunlight leads to factors such as 
drier soils and also creates a different growing environment. For 
example, the creation of roads changes the habitat by altering the 
distance of nesting and feeding habitat to the forest ``edge,'' 
increasing the amount of light exposure, and creating stress on 
(breeding) individuals in part due to noise and visual stimuli 
(Ben[iacute]tez-L[oacute]pez et al. 2010, p. 1,308).
Coca Cultivation
    Ongoing coca cultivation has had a significant impact on forest 
cover in Colombia (Armenteras et al. 2006, p. 355; Fjelds[aring] et al. 
2005, p. 205; Page 2003, p. 2; [Aacute]lvarez 2002, pp. 1,088-1,093). 
Colombia is one of the leading producers of coca, the plant species 
that provides the main ingredient of cocaine. Between 1998 and 2002, 
cultivation of illicit crops increased by 21 percent each year, with a 
parallel increase in deforestation of formerly pristine areas of 
approximately 60 percent ([Aacute]lvarez 2002, pp. 1,088-1,093). Much 
of Colombia's coca is grown by farmers because it generates more income 
than any other crop (Butler 2006, pp. 1-2). Illegal drug crops are 
cultivated within the great green macaw's range (BLI 2014b, p. 4). 
Large-scale coca production has moved into the extensive rainforests of 
the Choc[oacute] state, which is considered to be a biodiversity 
hotspot in northwest Colombia and in the range of the great green 
macaw.
    A 1990 United Nations study estimated that coca growers can make 
about $4,000 U.S. dollars per hectare (Tammen 1991, p. 12 in Page 2003, 
pp.

[[Page 60006]]

15-16). A farmer can only earn about $600 per hectare growing an 
alternative crop such as coffee, which is the most often cited 
potential substitute crop for coca (Page 2003, pp. 15-16). Page (2003, 
pp. 15-16) notes that production of coffee and tea requires 3 to 4 
years from planting to first harvest and then can only be harvested 
once per year, while coca can be harvested 8 months after it is planted 
and can be harvested every 90 days thereafter. The coca bushes 
themselves do not require much care and can be cultivated on plots of 
land that are much smaller than those required for crops other than 
coca (Tammen 1991, p. 6 in Page 2003, p. 16). Unfortunately, not only 
do coca crops displace native habitat and species assemblages that are 
important for the great green macaw, but they also deplete the soil of 
nutrients, which hampers regeneration following abandonment of fields 
(Van Schoik and Schulberg 1993, p. 21).
    Drug eradication efforts in Colombia have further degraded and 
destroyed primary forest habitat by using nonspecific aerial herbicides 
to destroy illegal crops (BLI 2007d, p. 3; [Aacute]lvarez 2005, p. 
2,042; C[aacute]rdenas and Rodr[iacute]guez Becerra 2004, p. 355; 
Oldham and Massey 2002, pp. 9-12). For example, in 2006, eradication 
efforts were undertaken on over 2,130 km\2\ (822 mi\2\) of land, which 
included spraying of 1,720 km\2\ (664 mi\2\) and manual eradication on 
the remaining land. These eradication efforts occurred over an area 2.7 
times greater than the net cultivation area (UNODC et al. 2007, p. 8). 
Herbicide spraying has introduced harmful chemicals into great green 
macaw habitat and has led to further destruction of the habitat by 
forcing growers to move to new, previously untouched forested areas 
([Aacute]lvarez 2007, pp. 133-143; BLI 2007d, p. 3; [Aacute]lvarez 
2005, p. 2042; C[aacute]rdenas and Becerra 2004, p. 355; Oldham and 
Massey 2002, pp. 9-12; [Aacute]lvarez 2002, pp. 1,088-1,093).
    The ecological impacts of coca production are significant. Farmers 
clear forest to plant coca seedlings. Not only does each hectare of 
crop production result in the clearing of roughly 1.6 ha (4 ac) of 
forest, this practice also results in secondary effects such as the 
pollution of land and local waterways with the chemicals used to 
process coca leaves, including kerosene, sulfuric acid, acetone, and 
carbide (Butler 2006, pp. 1-2).

Costa Rica

    Most of the research on this species has been conducted in Costa 
Rica, where a very small population of this species remains. Despite 
Costa Rica's progress in conservation of this species, the historical 
breeding area for this species in Costa Rica has been reduced by 90 
percent (Villate et al. 2008, p. 19; Chosset et al. 2004, p. 38). In 
2004, approximately 30 reproductive pairs remained in the wild in Costa 
Rica (Madriz-Vargas 2004, p. 4). Up until the 1960s, Costa Rica's human 
population was growing by approximately 4 percent annually (World Bank 
2011, unpaginated; Chun 2008, p. 6). Logging in the 1960s and 1970s 
decimated this species' habitat (Hardman 2011, p. 8). In the 1980s, the 
area near Puerto Viejo de Sarapiqui experienced severe deforestation 
and conversion to banana and pineapple plantations. By 1996, 52,000 ha 
(128,495 ac) of lowland forest had been converted to banana plantations 
(Brewster 2009, p. 8). The loss of forested area in the north has 
primarily been due to the production of livestock, forestry products, 
sugar cane, and (in more recent years) pineapple (Villate et al. 2008, 
p. 15).
    In the mid-1980s, policies changed from granting incentives for 
livestock and cattle ranching to reforestation for forest management. 
However, these incentives led initially to the clearing of forests for 
conversion to exotic species plantations. As a result, forestry in 
Costa Rica (and Panama) has been dominated by the use of exotic species 
such as Tectona grandis (teak) or Gmelina arborea (melina) (Schmidt 
2009, p. 10). This trend changed in 1986 with the Forestry Act 7472. In 
the 1990s, the government began to create incentives for small farm 
owners to establish and maintain native tree species plantations 
(Piotto et al. 2003, p. 427). By 1992, a project was implemented to 
improve the use of forested areas; however, it estimated that by this 
time only 5 percent of original forest area remained intact (Chassot et 
al. 2001 in Villate et al. 2008, p. 15). Reforestation projects began 
initially through an agreement between Costa Rica and Germany. The 
program was implemented by the Agribusiness Association and Forestry 
Producers (APAIFO) and the Cooperation for Forestry Development San 
Carlos (CODEFORSA).
    In Costa Rica's border zone with Nicaragua, Landsat TM satellite 
images from 1987, 1998, and 2005 showed a fragmented landscape with 
remnants of natural ecosystems, which has implications for the 
conservation of this species. The images identified several classes of 
cover and land use (natural forest, secondary forest, water, 
agriculture and pasture, banana and pineapple plantations, and bare 
ground) (Chassot et al. 2009, pp. 8-9). These researchers noted that 
the annual rate of deforestation was 0.88 percent for the 1987-1998 
period, and 0.73 percent for the 1998-2005 period, taking into 
consideration recovery of secondary forest. The researchers also noted 
that, in the area studied, deforestation rates were higher than 
national averages for the same time span (Chassot et al. 2009, p. 9).
    In the 1990s, plans to form the San Juan-La Selva Biological 
Corridor began in response to the significant decrease in habitat 
available to the great green macaw and its decline in population 
numbers. In 1993 and 1994, about 1,000 km\2\ (386 mi\2\) were 
identified as important nesting areas for this species in Costa Rica. 
In 2002, the San Juan-La Selva Biological Corridor, an area of 60,000 
hectares (148,263 ac), was established to protect the nesting sites and 
migration flyway of the great green macaw in Costa Rica, up to the 
Nicaragua border (Guedes 2004, p. 280). Although this corridor is in 
place, recent reports indicate that habitat degradation and other 
factors continue to affect the great green macaw (Monge et al. 2009, p. 
121).
    Costa Rica was the only country in Central America that had a 
positive overall increase in forest area during the period 2000-2005 
(FAO 2010, p. 19; FAO 2007). Intense efforts are under way in Costa 
Rica to conserve and recover this species, in part by addressing 
habitat degradation. In some areas, the commercial use of the almendro 
tree is now being replaced by synthetic material due to conservation 
efforts focused on the great green macaw. In some areas, landowners are 
being paid to protect and ``adopt'' almendro trees, and several 
ecotourism projects have developed using these trees and the macaws as 
part of the ecotourism attraction. As of 2009, 12 nesting trees had 
protection agreements (Brewster 2009, p. 10). Still, habitat 
degradation continues to impact the great green macaw (Villate et al. 
2008, p. 14), and even trees that are designated as protected are 
either cut down or targeted for poaching (Chun 2008). Logging still 
occurs in the remnant forests of both the northern zone of Costa Rica 
and southeast Nicaragua (Chassot and Arias 2011, p. 1; Monge et al. 
2009, pp. 128-129). Logging, while it may be illegal, has also been 
documented in the buffer zone of the Indio-Ma[iacute]z Biological 
Reserve (Monge et al. 2006, p. 10). The buffer zone is within the 
breeding range of the great green macaw and likely affects the species' 
viability. Additionally, both primary and regrowth forest in the San 
Juan-La Selva Biological Corridor

[[Page 60007]]

continue to be threatened by timber extraction and agricultural 
expansion (Chassot and Arias 2011, p. 1; Monge et al. 2009, pp. 128-
129).
Mining
    Gold mining may also affect conservation efforts for the great 
green macaw in Costa Rica. In 2001, the Ministerio del Medio Ambiente y 
Energ[iacute]a (MINAE) granted a mining concession (Resolution R-578-
2001-MINAE) in San Carlos to clear nearly 202 ha (500 ac) of old-growth 
rainforest for a project (Villate 2009, p. 57; http://www.infinito.co.cr and http://www.nacla.org, both accessed November 15, 
2011). The Crucitas mining project is located in the Northwest Corridor 
of San Juan-La Selva, a few miles from the San Juan River (which 
separates Costa Rica from Nicaragua). The Crucitas area is part of a 
major zone for bird conservation initiatives, partly implemented by 
BLI, that includes both the Water and Peace Biosphere Reserve and the 
San Juan-La Selva Biological Corridor (Chassot et al. 2009, p. 9), 
including the El Castillo extension. It is reported that 72 percent of 
the area that had been proposed for implementation of the project is 
forested and contains almendro tree (and consequently great green 
macaw) habitat. The company proposed to clearcut the area in order to 
establish the open pit mine.
    In adjacent Nicaragua, the area of influence of the mining project 
is also part of the buffer zone of the two reserves: San Juan River 
Biosphere Reserve and the Indio-Ma[iacute]z Biological Reserve. These 
areas contain features of endemism and species compositions that are 
unique (Sistema Nacional de [Aacute]reas de Conservaci[oacute]n (SINAC) 
2007 in Villate et al. 2008, p. 58). Although Crucitas is not part of 
the current nesting area of the great green macaw, it is only about 10 
km (3 mi) southeast of the historical distribution of the species. The 
mining activities are likely to affect the current population of the 
great green macaw by impacting its habitat as well as ongoing 
conservation efforts. The project lies within a geographical area that 
is of critical importance to the conservation of this species. 
Additionally, the removal of more primary forest cover would further 
reduce the ability to maintain connectivity along the San Juan-La Selva 
Biological Corridor, which continues to be subjected to fragmentation 
(Villate 2008, p. 58). As of November 2010, a court ruled that the 
open-pit gold mine was improperly permitted (http://centralamericadata.biz/en/article/home/Crucitas_Mining_Concession_Cancellation_Confirmed, accessed January 12, 
2012). However, prior to the court ruling, 121 ha (300 ac) of primary 
forest had already been cleared (http://www.santuariolapas.com/profile_003.html, accessed December 14, 2011). The ultimate impacts and 
outcome of the mining project are unclear; however, the species is and 
will continue to be impacted by pressures for resources that affect its 
habitat.

Ecuador

    Although the population of great green macaw is reported to be 
stable and slowly increasing in the Cerro Blanco Protected Forest, it 
is an extremely small population (Monge et al. 2009, p. 256). There are 
likely fewer than 100 individuals remaining in Ecuador. In this part of 
its range, three tree species are noted as crucial for the survival of 
the species: Lecythis ampla (salero) and Cynometra bauhiniaefolia 
(cocobolo) as primary food sources, and Cavanillesia platanifolia 
(pigio) as a nest tree (Horstman 2011 pers. comm. 2011). Logging, 
poaching, and illegal land settlements continue to occur in the great 
green macaw's range and are threats to the population in Ecuador, 
particularly in the Cerro Blanco Protected Forest (http://www.worldlandtrust-us.org, unpaginated; World Wildlife Fund 2011, p. 5; 
Horstman 2011, p. 12). Between 1960 and 1980, the human population in 
Ecuador grew from 4 to 10.2 million, which resulted in more than 90 
percent of Pacific lowland and foothill forest below 900 m (2,953 ft) 
being converted to agriculture (Dodson and Gentry 1991, p. 279). Much 
of the species' habitat was converted to plantations of bananas, oil 
palms, cacao, coffee, soybeans, and rice (ELAW 2005, p. 1; Dodson and 
Gentry 1991, p. 279).
    In 2002, the Government of Ecuador authorized the conversion of 
50,000 ha (123,553 ac) of tropical forest in the Choco region of 
western Ecuador into oil palm plantations (ELAW 2005, pp. 1-2). As of 
2005, 374 ha (924 ac) of native forests were being cut daily (Horstman 
2005, p. 8). Clearing forests for this monoculture crop has threatened 
thousands of endemic species and introduced dangerous pesticides to 
local ecosystems (Alb[aacute]n and C[aacute]rdenas 2007, p. 43). For 
example, in Esmeraldas Province, pesticides are used intensively in a 
36,000-ha (88,958-ac) area of oil palm plantations (ELAW 2005, pp. 1-
2). Local villages cite problems from the pesticides and effluents from 
the processing plants.
    The Food and Agriculture Organization of the United Nations (FAO) 
reported in 2010 that, in Ecuador, ``planted forests are predominantly 
composed of introduced species,'' such as rubber plantations and other 
nonnative species (FAO 2010, p. 93), which do not provide appropriate 
habitat and nutritional needs for the great green macaw. Despite these 
activities, due to the efforts of the ProForest Foundation--the NGO in 
charge of the reserve--the population in the Cerro Blanco forest 
preserve is reported to be stable (Horstman 2011, p. 17). The Cerro 
Blanco forest preserve is a small area that is being managed 
particularly for this species. It is jointly owned by the ProForest 
Foundation and a cement company, Holcim, as mitigation for its nearby 
limestone quarries. Reserve managers are converting former cattle 
pasture to native tree farms, which they use to help restore dry 
tropical forest in other locations, including a corridor to nearby 
patches of forested areas (Horstman 2009 pers. comm.). Despite the 
conservation efforts in place, logging, poaching, and illegal land 
settlement continue to affect the population in the Cerro Blanco 
Protected Forest (Horstman 2011, p. 17; Fundacion Pro-Bosque, undated, 
p. 3). A conservation strategy for this species recommends that a ban 
be instituted on the cutting and commercialization of the three tree 
species described above that were noted as crucial for the great green 
macaw's survival (Monge et al. 2009, pp. 256-258). However, 
deforestation, encroachment, and habitat degradation activities such as 
these continue (Horstman 2011, p. 17).
    Another threat to the macaw's population in this reserve is the 
rapid expansion of the city of Guayaquil. Squatter settlements develop 
on the city's outskirts and encroach the forest (Fundacion ProBosque 
undated, p. 3). Illegal settlements are a problem, and squatter 
communities have attempted to take over property within Cerro Blanco. 
The local NGO conducts educational awareness programs to mitigate these 
activities. An example of awareness campaign activities is educating 
the local communities about the effect on their water supply when they 
destroy forested areas (Horstman pers. comm. in Hardman 2011, p. 13). 
However, pressures to this species' habitat continue to impact the 
species.

Honduras

    In Honduras, threats have included illegal trafficking of this 
species and deforestation due to agriculture, cattle grazing, and 
logging (Devenish et al. 2009, p. 256). The threat of deforestation is 
particularly important because a

[[Page 60008]]

recent study found that 87 percent of Honduras is only suitable for 
forest (Larios and Coronado 2006, p. 13) due to its generally 
mountainous terrain. There is very little information available on the 
status of this species in Honduras, particularly scientific literature 
(Monge et al. 2009, p. 122). Only six papers on avian diversity and 
avian population surveys in Honduran forests were published between 
1968 and 2004 (Anderson et al. 2004, p. 456). However, we do know that 
the threats in Honduras are similar to those in other countries within 
the range of this species (McCann et al. 2003, pp. 321-322), and the 
most significant threat is deforestation. In 2008, the Departamento de 
[Aacute]reas Protegidas y de Vida Silvestre (DAPVS) in Honduras 
estimated that 80,000 ha (197,684 ac) of natural areas were being 
destroyed annually (DAPVS 2008 in Devenish et al., 2009 p. 256).
    The great green macaw is believed to exist in the R[iacute]o 
Pl[aacute]tano Biosphere Reserve within the watershed of the 
Pl[aacute]tano River (Monge et al. 2009, p. 8). The area is also known 
as the ``Mosquitia Hondure[ntilde]a,'' which is 500,000 ha (1,235,527 
ac) in size. The reserve serves as protection to the 100-km (62-mi) 
long Pl[aacute]tano River watershed in addition to protecting parts of 
the Paulaya, Guampu, and Sicre rivers (Devenish 2009, p. 256). Several 
indigenous tribes such as the Miskito, Tawahka, Pech, Gar[iacute]funas, 
and ``Mestizos'' use this area for their traditional livelihoods. 
Although this reserve was designated as a World Heritage Site, 
pressures to the reserve area for its resources continue (TNC 2011, 
unpaginated). In 2011, the R[iacute]o Pl[aacute]tano Biosphere Reserve 
was added to the list of World Heritage Sites in danger due to 
encroachment (UNEP-WCMC 2011, p. 1).
    In the R[iacute]o Pl[aacute]tano Biosphere Reserve of Honduras, the 
unregulated extraction of timber and mass production of bananas has 
caused an alarming decline of great green macaw populations (Devenish 
et al. 2009, p. 256). The deforestation in Honduras is occurring as a 
result of an increase in the human population, which requires clearing 
areas for home development as well as wood products (Devenish et al. 
2009, p. 256). The annual human population growth rate as of 2011 was 
estimated to be 1.09 percent (U.S. Department of State 2011, 
unpaginated). Palacios and Brus Laguna, towns on the coast 
approximately 5 km (3.1 mi) from the park on either side of the 
reserve, are likely contributing to the pressures such as agriculture 
and logging that are occurring illegally in the reserve.

Nicaragua

    In Nicaragua, great green macaws face reductions in populations due 
to illegal extraction of timber and agricultural expansion (McGinley et 
al. 2009, pp. 13, 33, 35; Jeffrey 2001, pp. 1-5). Overall, there is a 
lack of information about the status of the great green macaw 
population and its habitat in Nicaragua (Monge et al. 2010; Monge et 
al. 2009, pp. 52-53). However, a population of the great green macaw is 
known to occur in the Indio-Ma[iacute]z Biological Reserve, located in 
Nicaragua just across the San Juan River at the northeastern border of 
Costa Rica (Monge et al. 2009, p. 51), where suitable habitat for this 
species remains. This reserve, which is believed to be one of the few 
strongholds for the great green macaw, is nearly 264,000 ha (652,358 
ac) in size. It is likely that the Indio-Ma[iacute]z Biological Reserve 
contains extensive forest areas with high densities of almendro trees 
(Chun 2008, p. 94) and, therefore, is critical to this species' 
survival. Chun suggests that many areas in Nicaragua may exceed the 
minimum great green macaw nesting requirement of 0.20 trees per hectare 
within the breeding territory. Although the Indio-Ma[iacute]z 
Biological Reserve is considered one of Nicaragua's best preserved 
forested areas and has limited access, its buffer zone has recently 
been under assault from activities such as loggers in search of lumber 
and illegal farming of Elaeis guineensis (African palm) trees for 
biofuel (Chosset and Arias 2010, p. 3; Ravnborg et al. 2006, p. 2). As 
resources become scarcer in the buffer zones, illegal activities push 
farther into the lesser disturbed and lesser accessible areas. Despite 
the existence of this protected area, deforestation continues to occur.
    Deforestation is one of the major threats to biodiversity in this 
region; one steadily increasing form is the conversion of forest into 
agricultural or pastural lands (Chassot et al. 2006, p. 84). In 
Nicaragua, between 1990 and 2005, 1.35 million ha (3.34 million ac) of 
forested areas were converted to agriculture or were deforested due to 
other reasons such as logging (FAO 2010, p. 232; FAO 2007). Much of 
Nicaragua has protected status. In 2005, approximately 36 percent of 
Nicaragua's forested area was designated as protected or in some form 
of conservation status (FAO 2007). Additionally, in 2007, there were 72 
protected areas in Nicaragua's National System of Protected Areas 
(Castellon 2008, p. 19). However, 88 percent of Nicaragua's area 
designated as forest is privately owned (FAO 2010, p. 238) and, 
therefore, is not protected. Additionally, much of the logging that 
occurs is illegal and is not monitored (Pellegrini 2011, p. 21; 
Richards et al. 2003, p. 283).
    As an example, the Bosawas Reserve is one of the areas believed to 
contain great green macaws as well as suitable habitat for a viable 
population. It was designated a reserve in 1979, in response to the 
advance of the agricultural frontier (Cu[eacute]llar and Kandel 2005, 
p. 9). However, during the 1980s, the area was not managed; it was the 
battleground for the armed conflict between the Sandinistas and the 
Contras (Cu[eacute]llar and Susan Kandel 2005, p. 9). In October 1991, 
Bosawas was declared a National Natural Resource Reserve through 
Executive Decree No. 44-91. Despite its designation as a protected 
area, encroachment and habitat degradation still occur (McCann et al. 
2003, p. 322). In Bosawas, indigenous tribal communities have rights to 
use the forests under the Autonomy Statute of 1987 (Cu[eacute]llar and 
Kandel 2005, p. 11). As of 1998, the indigenous population was 
approximately 9,200 in or near the Bosawas reserve (Stocks et al. 2007, 
p. 1,497). In 2005, the Nicaraguan Government granted land titles to 86 
indigenous Miskitu and Mayangna groups in Bosawas and contiguous 
indigenous areas (Stocks et al. 2007, p. 497). Generally, these 
indigenous communities manage the forests well and want to maintain 
their traditional way of life. However, ``mestizo'' communities were 
encouraged to settle in the area that is now the reserve's buffer zone 
during the period when lands were being converted to plantations. Both 
the mestizo and indigenous communities depend on access to land to 
ensure their livelihoods. However, the mestizo communities convert 
primary forest to agricultural or livestock uses (Cu[eacute]llar and 
Kandel 2005, p. 13), while the indigenous communities have less impact 
on the ecosystem. Land rights disputes are common in these areas, and 
land use rights are often unclear. The Government of Nicaragua is 
attempting to manage these issues (Pellegrini 2011, p. 21), but 
conflict and practices that degrade the great green macaw's habitat 
persist both in the Bosawas Reserve and in other areas within the range 
of the species.
    One of the factors contributing to deforestation in this area is a 
high rate of poverty (Pacheco et al. 2011, p. 4). Nicaragua is the 
poorest country in Central America (CIA World Factbook 2014). In part, 
due to the high rate of poverty, the great green macaw continues to 
face threats to its habitat.

[[Page 60009]]

Communities living within the range of the great green macaw practice 
unsustainable activities, such as conversion of habitat to agriculture 
or logging, which contribute to deforestation of the species' remaining 
habitat in Nicaragua (McGinley 2009, p. 36; Castellon 2008, pp. 21, 30; 
Richards et al. 2003, p. 282). Much of the Indio-Ma[iacute]z Biological 
Reserve is described as being intact and unlogged (Chun 2008, p. 116). 
Despite this, some loggers cross the border into Nicaragua to harvest 
the almendro tree (Schmidt 2009, p. 16; Chassot et al. 2006, p. 84). 
Anecdotal reports indicate that Costa Rican loggers pay Nicaraguan 
farmers about $15 for each almendro tree, bring the logs to Costa Rica, 
and sell them for about $1,450 in Costa Rica (Arias 2002, p. 4). 
Because incomes in the Bosawas region of Nicaragua were found to 
average under $800 per family per year (Stocks et al. 2007, p. 1,498), 
the almendro trees are quite valuable. Consequently, a binational 
biological corridor between Nicaragua and Costa Rica was proposed in an 
attempt to prevent the extinction of the almendro tree (Chassot et al. 
2006, p. 84). Although this corridor exists and efforts are in place 
(refer to discussion under Factor D, below) to mitigate border issues 
(Hernandez et al., undated, pp. 1-14) in this region, habitat 
degradation continues.

Panama

    In Panama, this species is believed to primarily exist in the 
Dari[eacute]n region, which borders northern Colombia (Angeher 2004, in 
litt.). Deforestation was estimated to exceed 30 percent of the 
species' original range in Panama (Angehr 2004, in litt.). Although 
there is limited information available on the threats affecting great 
green macaw populations in Panama, deforestation is known to occur 
within this species' range (Monge et al. 2009, p. 68; Angehr 2004, in 
litt.). Conflict regarding land rights of indigenous communities has 
become one of the most critical issues in the Dari[eacute]n region. The 
most significant threats to tropical forests in Panama overall include 
road construction and road improvement, especially in the Dari[eacute]n 
region, and agricultural expansion, particularly in the Dari[eacute]n 
and Bocas del Toro regions, which results in increased access to 
forests (Parker et al. 2004, p. V-2). Roads have been found to be one 
of the leading causes of global biodiversity loss (Ben[iacute]tez-
L[oacute]pez et al. 2010, p. 1,307). The construction of the Pan-
American Highway and other roads are affecting the Dari[eacute]n forest 
area (TNC 2011, p. 1). When roads are constructed, they increase access 
to previously inaccessible areas. This leads to more pressures on the 
forested areas, such as conversion to agriculture, competition for 
resources (such as the extraction of plant species that may be consumed 
by the great green macaw), and more logging.
    A 2006 report indicated that the advance of the agricultural 
frontier and ``spontaneous colonization'' occurring at a rate of 50,000 
to 80,000 ha (123,500 to 197,700 ac) per year is rapidly shrinking 
Panama's forests and protected areas (McMahon et al. 2006, p. 8). Prior 
to its formal designation in 1990, La Amistad National Park, which 
spans the border between Costa Rica and Panama, experienced impacts 
from cattle ranching, timber extraction, burning, and illegal 
settlements (UNEP-WCMC 2011, p. 7). Trails, human encroachment, roads, 
grazing, and hunting continue in this area and affect this species' 
habitat (TNC 2012, unpaginated; UNEP-WCMC 2011, p. 7). Soil and water 
resources have been depleted due to traditional agricultural practices 
and inadequate conservation measures. Indigenous production systems, 
with their low-intensity land use, long rotation periods, and plentiful 
forests for hunting and gathering, are increasingly becoming 
unsustainable due to economic pressures. These indigenous production 
systems are being replaced by farming systems that emphasize 
monoculture without rotation, which leads to depleted soils and 
encourages greater expansion of the agricultural frontier. These 
threats are exacerbated by rural poverty that drives populations in 
search of areas with high levels of globally significant biodiversity 
(Pacheco et al. 2011, pp. 4, 18). As a result of competition for 
resources, many farmers and indigenous people have emigrated to the 
Dari[eacute]n and Bocas del Toro provinces, where the great green macaw 
is believed to exist in larger numbers than in other parts of the 
species' range. Unsustainable land practices, the lack of capacity by 
both public and private stakeholders to encourage sustainable land use, 
infrastructure development, and the lack of management plans further 
exacerbate the degradation of this species' habitat.
    Dari[eacute]n forests are under pressure from the expanding 
agricultural frontier and related colonization (TNC 2011, p. 1; McMahon 
2006, p. 8). The region's human population is growing at a rate of 
about 5 percent a year. Loss of forest cover is often linked to 
agricultural expansion, which often follows new or improved roads, and 
which results in increased access to forests. Slash-and-burn 
agriculture has resulted in huge tracts of deforested land. Other 
factors that affect the stability of great green macaw populations 
include the National Authority for the Environment's (ANAM) inability 
to fund programs for protected areas and buffer zones, and the 
extraction of other minerals and building materials, whether legal or 
illegal (Angehr et al. 2009, p. 291). Logging and mining is legally 
restricted in the area; however, logging still occurs outside the 
Dari[eacute]n reserve, and the practice encroaches on remaining forest 
cover in the buffer zone. Problems in or adjacent to protected areas 
include illegal clearing for development, agriculture, and cattle 
grazing; road construction; and extraction of minerals or construction 
materials (Devenish et al. 2009b, p. 291).
    The presence of gold mines in the Dari[eacute]n Region, 
particularly the Cerro Pirre area, was also indicated to be a threat to 
the species. Significant mining activities in this area were conducted 
prior to the 18th century. The clearing of forests to create roads for 
mining facilitates the transport of materials and personnel in and out 
of the mining zones (Robbins et al. 1985, pp. 200, 202). Roads 
exacerbate deforestation practices such as logging and conversion to 
agriculture or other land uses, as well as colonization. This area is 
now an ecotourism site; as of 1985, there is now second-growth forest 
recovery from the gold mines that had been abandoned during the 18th 
century. It does not appear that mining in this area still occurs, and, 
therefore, mining is not currently impacting the species.

Summary of Factor A

    The global population of great green macaws is decreasing due to 
the loss of much of the older forested areas, thus reducing high-
quality habitat for this species, and relegating it to relatively small 
and isolated patches throughout its range; however, suitable habitat 
remains in some protected areas in Central and South America. Habitat 
degradation poses a significant threat throughout the range of the 
great green macaw, which is especially vulnerable to the effects of 
isolation and fragmentation because it tends to mate for life, it has a 
small clutch size and specialized habitat requirements, and its 
populations are small and decreasing.
    The great green macaw is naturally associated with unfragmented, 
mature, forested landscapes, and is considered a habitat specialist 
that selects areas of contiguous mature forest in Central America and 
parts of northern South America (Monge et al. 2009; Madriz-Vargas 2004, 
p. 7). This species requires

[[Page 60010]]

large areas for its feeding requirements and is not well adapted to 
fragmented landscapes. Deforestation results in fragmented forests with 
high ratios of edge to forested area, and the original biodiversity 
upon which this species depends is lost. Greater exposure of soil to 
direct sunlight leads to factors such as drier soils and also creates 
an altered growing environment. Because there are fewer remaining 
older, complex forest stands providing adequate habitat for breeding, 
feeding, and nesting, great green macaw populations are in decline. The 
great green macaw is threatened by the impacts of both past and current 
habitat loss, including ongoing habitat modification that results in 
poor quality and insufficient forest habitats, habitat fragmentation, 
and isolation of small populations. The ability of the great green 
macaw to repopulate an isolated patch of suitable habitat following 
decline or extirpation is particularly unlikely due to the species' 
large home range requirements, and this is exacerbated by its small 
overall population size and the large distances between the remaining 
primary forest fragments. Despite the existence of the binational 
corridor in Nicaragua and Costa Rica and a multitude of conservation 
efforts, we find that the present or threatened destruction, 
modification, or curtailment of habitat is a threat to the great green 
macaw now and in the future.

B. Overutilization for Commercial, Recreational, Scientific, or 
Educational Purposes

    Because this species has an extremely small and fragmented 
population, poaching, while apparently uncommon, remains a concern 
(Botero-Delgadillo and P[aacute]ez 2011, p. 13; Monge et al. 2009, pp. 
26, 40, 106). Removal of this species from the wild has a significant 
detrimental effect to this species because this species tends to mate 
for life and only produces 1 or 2 eggs annually. The species has been 
heavily poached in the wild historically and is still trafficked for 
the pet trade in Honduras and Nicaragua (Anderson 2004, p. 453; http://www.lafeberconservationwildlife.com/?p=1714, accessed December 14, 
2011). Although there are no known current reports of poaching in all 
parts of its range, poaching was raised as a concern at the 2008 
workshop held in Costa Rica on this species (Monge et al. 2009, 
various). After regulatory mechanisms such as CITES and the WBCA were 
put into place, particularly since 1992 when the WBCA went into effect, 
much of the legal trade in the great green macaw declined (see 
discussion of military macaw for more information about WBCA) (UNEP-
WCMC CITES trade database, accessed September 6, 2011). The great green 
macaw was listed in CITES Appendix II, effective June 6, 1981, and was 
transferred to Appendix I, effective August 1, 1985. Most of the 
international trade in great green macaw specimens consists of live 
birds.
    Data obtained from the United Nations Environment Programme-World 
Conservation Monitoring Center (UNEP-WCMC) CITES Trade Database show 
that, during the 4 years the great green macaw was listed in Appendix 
II, 26 live great green macaws (and an additional eight feathers) were 
reported to UNEP-WCMC as (gross) exports. In analyzing the data, it 
appears that several records may be overcounts due to slight 
differences in the manner in which the importing and exporting 
countries reported their trade. It is likely that the actual number of 
live great green macaws in international trade during this period was 
22. All of the live birds were reported with the source ``unknown.'' 
Exports from range countries included six live birds from Panama and 
five live birds from Nicaragua (UNEP-WCMC 2011).
    During the more than 28 years following the transfer of the species 
to Appendix I (August 1985 through December 2013, the last year for 
which complete data were available at the time the following numbers 
were compiled), the UNEP-WCMC database shows 920 live birds in 
international trade. However, because it is some over-counts likely 
occurred in the database due to slight differences in the manner in 
which the importing and exporting countries reported their trade, it is 
likely that the actual number of live great green macaws in 
international trade during this period was 831 (U.S. CITES Management 
Authority 2015). Of these, 776 were reported to be captive-bred or 
captive-born, 5 were reported as wild, and 15 were reported as ``pre-
Convention.'' The source of the remaining live birds is unknown. 
Exports of live birds from range countries included 17 from Costa Rica, 
10 from Ecuador, 12 from Nicaragua, and 6 from Panama. Note also that 
some of these birds may be personal pets that are counted more than 
once.
    Historically, the pressure to remove this species from the wild for 
the pet trade has contributed significantly to the decline in 
population numbers for this species. Poaching continues to occur in 
this species' range, particularly in Nicaragua (Castellon 2008, pp. 20, 
25; Kennedy 2007, pp. 1-2; BLI 2007, p. 1). The majority of information 
available for Central America regarding poaching and the sale of parrot 
species were focused in Nicaragua (Herrera-Scott 2004, pp. 1-2). A 
study published in 2004 assessed the origin and local sale and export 
of parrots and parakeets in Nicaragua (Herrera-Scott 2004, pp. 1-2), 
and focused on the buffer zone of the Indio-Ma[iacute]z Biological 
Reserve, a critical area for the great green macaw. The study followed 
the marketing chain from rural areas to the capital city. Most of the 
wildlife trade was found to occur in Managua. As of 2000, poaching was 
still occurring in the buffer zone of the Indio-Ma[iacute]z Biological 
Reserve (Herrera-Scott 2004, p. 6). An estimated 7,205 parrots were 
sold during that year (Herrera-Scott 2004, p. 1). The legal export of 
wildlife species from Nicaragua in general decreased significantly 
between 2002 and 2006 (McGinley 2009, p. 16). Despite the decrease in 
legal trade, in 2007, a number of parrot species could be still found 
for sale along roads to tourists (Kennedy 2007, pp. 1-2; BLI 2007, p. 
1). Nicaragua is the poorest country in Central America and the second 
poorest in the Hemisphere, and has widespread underemployment and 
poverty (CIA World Factbook 2011, unpaginated; FAO 2011, p. 1). 
Approximately 17 percent of its population lives in extreme poverty 
(Castellon 2008, p. 21). Many of Nicaragua's citizens live in rural 
areas where they usually earn a living from agriculture and fishing, 
and the sale of a parrot can significantly increase their earnings. As 
mentioned above under the Factor A discussion, incomes in the Bosawas 
region of Nicaragua were found to average under $800 per family per 
year as of 2007 (Stocks et al. 2007, p. 1,498). The great green macaw 
was found for sale at an average of $200 to $400 U.S. dollars (USD) 
(Fundacion Cocibolca in BLI 2007, p. 1). For perspective, in the United 
States, captive-bred specimens can sell for up to $2,500 USD (Basile 
2009, p. 6). The high commercial value, especially in relation to the 
average family income, indicates that it is still worthwhile to poach 
and sell this species. Due to the extreme poverty in Central America, 
particularly in Nicaragua, and due to the high commercial value of 
great green macaws, poaching continues to be a significant concern for 
this species.
    Poaching can be intertwined with habitat destruction (Factor A). 
Some poachers still cut down trees to obtain nestlings (Hardman 2011, 
p. 13; Chun 2008, p. 105). This practice of cutting down trees to 
remove nestlings is particularly devastating to small populations 
reliant upon certain types

[[Page 60011]]

and sizes of nesting trees. Not only are poachers removing vital 
members of the population, they are destroying a nest site that may 
have taken a breeding pair several years to find and cultivate. One 
study looked at 51 nest sites that had been identified between 1994 and 
2003 (Chun 2008, p. 105). The study evaluated potential habitat by 
examining the presence and density of almendro trees by aerial survey. 
It examined portions of two protected areas--the San Juan-La Selva 
Biological Corridor and the Maquenque National Wildlife Refuge (Chun 
2008, p. 117). Of 51 nest sites, 10 trees had been cut by the end of 
the survey period. In some cases, the nests had been deliberately cut 
even after the tree had received protection status and had been 
distinguished as a nesting tree with a plaque. Nest destruction has 
also been reported in Ecuador (Bergman 2009, pp. 6-8), where it is 
estimated to have an extremely small population. Another study 
confirmed the presence of nest destruction, although this was a 
different parrot species, and found an average of 21 nests was 
destroyed per poaching trip (Gonzalez 2003, p. 443).
    Poaching for the pet bird trade can destroy pair bonds, remove 
potentially reproductive adults from the breeding pool, and have a 
significant effect on small populations (Kramer and Drake 2010, pp. 
511, 513). This is in part because this species mates for life, is 
long-lived, and has low reproductive rates. These traits make them 
particularly sensitive to the effects of poaching (Lee 2010, p. 3; 
Thiollay 2005, p. 1121; Wright et al. 2001, p. 711). In some areas in 
Costa Rica, there were no recent reports of nest poaching due to 
conservation efforts (Villate et al. 2008, p. 23). However, despite 
conservation efforts in place, the conservation workshop for Ara 
ambiguus held in 2008 indicated that poaching of this species is still 
a concern throughout its range (Monge et al. 2009, pp. 18, 26, 29, 40).

Summary of Factor B

    Conservation efforts by various entities working to ensure the 
long-term conservation of the great green macaw may result in its 
population slowly increasing (Monge et al. 2010, pp. 12-13). However, 
overall, the best available information indicates that the population 
is still declining (Botero-Delgadillo and P[aacute]ez 2011, p. 91; 
Monge et al. 2009). The species still faces threats such as habitat 
loss and poaching. Often, there is a lag time after factors have acted 
on a species (i.e., poaching and habitat loss) before the effect is 
evident (Sodhi et al. 2004, p. 325). Even though the great green macaw 
is listed as an Appendix-I species under CITES and commercial 
international trade is now significantly reduced, there is still 
concern about the illegal capture of this species in the wild. This 
species is desirable as a pet, and its native habitat is in 
impoverished countries, where the sale of an individual bird can 
significantly increase an individual's income. Despite regulatory 
mechanisms in place, poaching is lucrative and still occurs. 
Additionally, because each population of great green macaws is small, 
with possibly between 10 to 500 individuals (Monge et al. 2010, pp. 21, 
22), poaching is likely to have a significant effect on the species. 
The populations are distributed widely throughout the range of the 
species (see Figure 3) and are highly fragmented, and the amount of 
interaction between populations is unknown but likely infrequent. Based 
on the best available information, we find that overutilization, 
particularly due to poaching, is a threat to the great green macaw 
throughout its range now and in the future.

C. Disease or Predation

    We have no evidence of significant adverse impacts to wild 
populations of great green macaws due to disease. Diseases are a normal 
occurrence within wild populations. They do not occur to an extent that 
they are a threat to this species, particularly because the populations 
are widely dispersed, which provides an element of resiliency to the 
overall population. We conclude, based on the best available scientific 
and commercial information, that disease is not a threat to the great 
green macaw now or in the future.
    In addition, we have no information indicating that predation 
threatens the great green macaw. This is the second largest New World 
macaw, and the best available information does not indicate that 
predation is a factor that negatively affects this species. While 
predators undoubtedly have some effect on fluctuations in great green 
macaw numbers, there is no evidence to suggest that predation has 
caused or will cause long-term declines in the great green macaw 
population. Therefore, we have determined that this factor does not 
pose a threat to the great green macaw, now or in the future.

D. The Inadequacy of Existing Regulatory Mechanisms

    Regulatory mechanisms affecting this species that we evaluated 
could potentially fall under categories such as wildlife management, 
parks management, or forestry management. We primarily evaluated these 
regulatory mechanisms in terms of nationally protected parks because 
this is where this species generally occurs. A summary of the status of 
forest policies, regulatory mechanisms, and laws in the range countries 
of the great green macaw is below. The most authoritative source for 
assessing the state of forests is the United Nations Food and 
Agriculture Organization's Forest Resources Assessment (FAO) (Chomitz 
et al. 2007, p. 42). FAO's 2010 study found that each range country for 
this species has a national forest law, policy, or program in place, 
and Table 1 indicates the year it was last evaluated. However, the 
study found that few forest policies at the subnational level (such as 
jurisdictions equivalent to states in the United States) exist in these 
countries.

                                      Table 1--Adapted From FAO Global Forest Resource Assessment 2010, pp. 302-303
--------------------------------------------------------------------------------------------------------------------------------------------------------
                                   National forest policy                 National forest program                         Forest law national
                               -------------------------------------------------------------------------------------------------------------------------
            Country                                                                                                                         Subnational
                                      Exists          Year          Exists          Year         Status         National-type      Year        exists
--------------------------------------------------------------------------------------------------------------------------------------------------------
Colombia......................  Yes..............       1996  Yes..............       2000  Under revision..  Incorporated in        1974  No.
                                                                                                               other law.
Costa Rica....................  Yes..............       2000  Yes..............       2001  Under revision..  Specific forest        1996  No.
                                                                                                               law.
Ecuador.......................  Yes..............       2002  Yes..............       2002  In                Specific forest        1981  No.
                                                                                             implementation.   law.
Honduras......................  Yes..............       1971  Yes..............       2004  In                Specific forest   .........  No.
                                                                                             implementation.   law.
Nicaragua.....................  Yes..............       2008  Yes..............       2008  In                Specific forest        2003  Yes.
                                                                                             implementation.   law.
Panama........................  Yes..............       2003  Yes..............       2008  Unclear.........  Specific forest        1994  No.
                                                                                                               law.
--------------------------------------------------------------------------------------------------------------------------------------------------------


[[Page 60012]]

    In 2007, FAO noted that many countries (in the range of the great 
green macaw) had enacted new forest laws or policies within the past 15 
years, or had taken steps to strengthen their existing legislation or 
policies. Among countries that had enacted new forest legislation were 
Costa Rica, Honduras, Nicaragua, Panama, Colombia, and Ecuador (FAO 
2007, p. 43). Despite the existence of these laws and policies, the 
populations of the great green macaw are still negatively affected by 
habitat loss, encroachment, and, to a lesser extent, poaching.

Parks and Habitat Management

    Throughout this species' range, we found that many of the threats 
that occur to this species are the same or similar. Threats generally 
consist of various forms of habitat loss or degradation (see Factor A 
discussion, above). Each range country for this species has protections 
in place, but for reasons such as limited budgets and limited 
enforcement capabilities, the laws and protections are generally not 
able to adequately protect the species. Our analysis of regulatory 
mechanisms is discussed essentially on a country-by-country basis, 
beginning with Colombia, and is summarized at the end.

Colombia

    Colombia has enacted numerous laws to protect species and their 
habitats. This species exists predominantly in areas that are 
protected, and Colombia has several laws that pertain to protected 
areas. Some of these laws include:

 Natural Resources and Decree Law number 2811/74.
 Decree 1974/89: Regulation of Article 310 of Decree 2811, 
1974, on integrated management districts of natural renewable 
resources.
 Law number 99/93: Creates the Ministry of the Environments and 
the National Environmental System.
 Law number 165/94: Biological Diversity Treaty.
 Decree 1791/96: Establishment of the Forest Use Regime.

A list of legislation that applies to protected areas in Colombia is 
available at http://www.humboldt.org.co/ingles/en-politica.htm and at 
http://www.regulations.gov in Docket No. FWS-R9-ES-2011-0101. A 
discussion of Colombia's regulatory mechanisms with respect to the 
great green macaw follows.
    The great green macaw is listed as vulnerable on Colombia's Red 
List (Renjifo et al. 2002, p. 524). Resolution No. 584 of 2002 provides 
a list of Colombian wildlife and flora that are considered 
``threatened.'' Colombia defines threatened as those species whose 
natural populations are at risk of extinction if their habitat, range, 
or the ecosystems that support them have been affected by either 
natural causes or human actions. Threatened species are further 
categorized as critically endangered, endangered, or vulnerable. 
Colombia defines a critically endangered species as one that faces a 
very high probability of extinction in the wild in the immediate 
future, based on a drastic reduction of its natural populations and a 
severe deterioration of its range. An endangered species is one that 
has a high probability of extinction in the wild in the near future, 
based on a declining trend of its natural populations and a 
deterioration of its range. A vulnerable species is one that is 
described as not in imminent danger of extinction in the near future, 
but it could be if natural population trends continue downward and 
deterioration of its range continues (EcoLex 2002, p. 10).
    Colombian Law No. 99 of 1993 created the Ministry of the 
Environment and Renewable Natural Resources and the National 
Environmental System (SINA). SINA sets out the principles governing 
environmental policy in Colombia, and provides that the country's 
biodiversity is protected and used primarily in a sustainable manner 
(Humboldt Biological Resources Research Institute 2011, unpaginated; 
EcoLex 1993, p. 2). SINA is a set of activities, resources, programs, 
and institutions that allow the implementation of environmental 
principles. Consistent with the Constitution of 1991, this management 
system was intended to be decentralized. However, an environmental 
assessment study conducted for the World Bank in 2006 found that 
Colombia's current decentralized system is inadequate as implemented 
(Blackman et al. 2006, p. 15). Although Law 99 assigns the role of 
leading and coordinating environmental management in Colombia to the 
Ministry of Environment (Ministerio del Medio Ambiente, MMA), 
Colombia's Autonomous Regional Corporations (CARs) have the role of 
implementing environmental laws (Blackman et al. 2006, pp. 39-40, 42). 
CARs have responsibility for both management of natural resources and 
economic development (Ministry of Environment et al. 2002).
    In 2006, an analysis of the effectiveness of Colombia's CARs was 
conducted for the World Bank. In Blackman et al. 2006's analysis, they 
reported that many individuals both inside and outside the government 
felt there was a lack of effectiveness of SINA. For example, Colombia's 
efforts to eradicate the coca trade has not been effective at reducing 
the amount of coca being cultivated (Page 2003, p. 2; also see The 
present or threatened destruction, modification, or curtailment of its 
habitat or range). In addition to not adequately addressing the coca 
cultivation, which destroys the great green macaw's habitat, aerial 
fumigations of the coca crop have destroyed banana fields and polluted 
the environment (Page 2003, p. 2). The effectiveness of these regional 
management groups varied; the study found that the effectiveness was 
correlated with the CARs' age, geographic size, and level of poverty 
(Blackman et al. 2006, p. 16). Due to the decentralized structure, CARs 
were found to be ineffective at environmental management in Colombia 
(Blackman et al. 2006, p. 14).
    This species' habitat occurs to some extent in areas designated as 
protected by SINA, including five national parks (Rodr[iacute]guez-
Mahecha 2002a). Two parks are particularly significant: Kat[iacute]os 
National Park and Utr[iacute]a National Park. Although this species 
likely exists in at least these two parks (Botero-Delgadillo and 
P[aacute]ez 2011, p. 92), no protective measures have been actually 
implemented to curb human impacts on the species' habitat by the 
indigenous and farming residents within these protected parks (Botero-
Delgadillo and P[aacute]ez 2011, p. 92). Cultivation of plants for 
cocaine production is known to occur within the boundaries of 
Kat[iacute]os National Park. The cultivation of illegal crops 
(particularly coca) poses additional threats to the environment beyond 
the destruction of montane forests (Balslev 1993, p. 3). Coca crop 
production destroys the soil quality by causing the soil to become more 
acidic, depletes the soil nutrients, and ultimately impedes the 
regrowth of secondary forests in abandoned fields (Van Schoik and 
Schulberg 1993, p. 21; also see The present or threatened destruction, 
modification, or curtailment of its habitat or range discussion, 
above). As of 2007, Colombia was the leading coca producer (United 
Nations Office of Drugs and Crime (UNODC) et al. 2007, p. 7). Since 
2003, cocaine coca cultivation has remained stable at about 800 km\2\ 
(309 mi\2\) of land under cultivation (UNODC et al. 2007, p. 8). This 
activity continues to degrade and destroy great green macaw's habitat. 
With respect to Utr[iacute]a National Park, little to no information is 
known about the status of the species in

[[Page 60013]]

this area (Botero-Delgadillo and P[aacute]ez 2011, p. 91). Although it 
is extremely remote, human communities reside within and around the 
park, and continue to use the resources within the park.
    Despite Colombia's numerous laws and regulatory mechanisms to 
administer and manage wildlife and their habitats, the great green 
macaw continues to face many threats to its habitat. There is little 
information available about the species (Botero-Delgadillo and 
P[aacute]ez 2011, p. 90), and the most recent information indicates 
that no conservation action has been proposed for this species (Botero-
Delgadillo and P[aacute]ez 2011, p. 88). On-the-ground enforcement of 
existing wildlife protection and forestry laws, and oversight of the 
local jurisdictions implementing and regulating activities, are 
ineffective at mitigating the primary threats to the great green macaw. 
As discussed under The present or threatened destruction, modification, 
or curtailment of its habitat or range (above), habitat destruction, 
degradation, and fragmentation continue throughout the existing range 
of the great green macaw. Therefore, we find that the existing 
regulatory mechanisms currently in place are inadequate to mitigate the 
primary threats of habitat destruction to the great green macaw in 
Columbia.

Costa Rica

    In Costa Rica, there are more than 30 laws related to the 
environment (Peterson 2010, p. 1). A list of the environmental laws in 
Costa Rica is available at: http://www.costaricalaw.com/costa-rica-environmental-laws.html. As deforestation is the most significant 
factor affecting the great green macaw, some laws applicable to the 
conservation of the great green macaw are:

 Law No. 2790 Wildlife Conservation Law (``Ley De 
Conservaci[oacute]n De La Fauna Silvestre,'' July 1961).
 Law No. 7317 Wildlife Conservation Law (``Ley De 
Conservaci[oacute]n De La Vida Silvestre,'' December 1992).
 Law 7554 Law of the Environment (``Ley Org[aacute]nica del 
Ambiente,'' October 1995).
 Law No. 7575 Forestry Law (``Ley Forestal,'' February 1996).
 Law 7788 Biodiversity Law (In 1998, the National System of 
Conservation Areas (SINAC) was created through this law (Canet-Desanti 
2007 in Villate et al. 2008, p. 24).

    In the early 1990s, Costa Rica had one of the highest deforestation 
rates in Latin America (Butler 2012, p. 3). Forest cover in Costa Rica 
steadily decreased from 85 percent in 1940, to around 35 percent today, 
according to the FAO's State of the World's Forests (Butler 2012, 
unpaginated; FAO 2010, pp. 227, 259; FAO 2007). Historically, clearing 
for agriculture, particularly for coffee and bananas, in addition to 
cattle pastures was the main reason for Costa Rica's rainforest 
destruction. During the 1970s and early 1980s, vast expanses of 
rainforest had been burned and converted to cattle pastures. Today, 
although deforestation rates of natural forest have dropped 
considerably, Costa Rica's remaining forests still experience illegal 
timber harvesting (in protected areas) and conversion to agriculture 
(in unprotected zones) (Butler 2012, unpaginated; Monge et al. 2009, p. 
121; FAO 2007). Despite its abundance of conservation legislation, 
Costa Rica has undergone significant periods of deforestation (Butler 
2012, unpaginated; FAO 2007, p. 38), which have had a severe effect on 
the great green macaw.
Almendro Tree Protection
    In Costa Rica and Nicaragua, the great green macaw is highly 
dependent on the almendro tree. This tree species is now protected by 
law in Costa Rica; cutting any almendro tree over 120 cm (47.2 in) or 
less than 70 cm (27.6 in) in diameter is prohibited (Rainforest 
Biodiversity Group 2008, p. 1). The remaining Costa Rican populations 
of almendro trees are concentrated in the northeastern corner of the 
country from the San Juan River south to Braulio Carrillo National Park 
(Hanson 2006, p. 3). Although little forest remains undisturbed in this 
region, many almendro trees were left standing in fragments or 
pastures, partly due to the extremely dense nature of the tree's wood 
and the difficulty in cutting down these trees.
    As a result of the great green macaw's dependence on almendro 
trees, conservation efforts for the great green macaw have focused on 
this tree species. A decree was enacted in 2001 to limit extraction of 
the almendro tree. Harvest was temporarily suspended until a study 
could be conducted to evaluate the status of this primary food and 
nesting source in relation to the great green macaw (Chosset et al. 
2002, p. 6). According to Costa Rican legislation (Decree No 25167-
MINAE), the removal or logging of almendro trees had been illegal in 
the area between the San Carlos and Sarapiqui Rivers (Madriz-Vargas 
2004, p. 9). The objective of the restrictions placed on extraction of 
almendro trees was to increase the number of nesting sites for the 
great green macaw and to prevent the tree from becoming extinct; 
however, forest clearings continued to occur at an alarming rate due to 
the lack of resources to protect biological reserves (Madriz-Vargas 
2004, p. 8). For example, researchers reported in 2003 that, of the 60 
great green macaw nests identified since the great green macaw 
conservation project was initiated in 1994, 10 had been cut down by 
forest engineers working in forest management plans (Monge and Chassot 
2003, p. 4). In 2008, Costa Rica's Supreme Court stated that MINAE must 
abstain from the continuation or initiation of the use, exploitation, 
or extraction of the almendro tree (Chun 2008, p. 113). In Costa Rica, 
fines for those who cut down almendro trees have been proposed as a 
measure, although penalties reportedly have not been instituted 
(Botero-Delgadillo and P[aacute]ez 2011, p. 92).
Great Green Macaw Conservation
    In the two core areas where the great green macaw exists in Costa 
Rica, conservation activities are under way, and the breeding 
populations are being closely monitored. Quebrada Grande is a 
community-operated, 119-ha (294-ac) reserve in the center of great 
green macaw habitat. Additionally, the National Green Macaw Commission 
was formed in 1996 to protect and manage this species' habitat. This 
commission was formed in response to the severe decline of the great 
green macaw population, and included 13 government agencies, NGOs, and 
the Sarapiqu[iacute] Natural Resources Commission (CRENASA). This 
conservation effort was formalized by Executive Order No. 7815-MINAE of 
1999. The group served as an advisory body to MINAE regarding 
environmental issues in the northern zone of Costa Rica that affect the 
great green macaw (Chassot and Monge 2008 in Villate et al. 2008, p. 
22). Conservation efforts are still in progress; in 2008, a workshop 
was held to bring together species experts and government officials to 
identify priorities and goals in order to conserve the species (Monge 
et al. 2009, entire).
    Additionally, a corridor was created in 2001, with the goal of 
maintaining connectivity and biodiversity between protected areas in 
southeastern Nicaragua, the Protected Conservation Area Arenal Huetar 
North (ACAHN), and Conservation Area of the Central Volcanic Cordillera 
(ACCVC) in Costa Rica. The primary purpose was to promote the creation 
of protected wilderness and encourage habitat protection necessary to 
preserve and

[[Page 60014]]

increase the great green macaw population (Villate et al. 2008, p. 24).
    In 2005, the Maquenque National Wildlife Refuge (MNWR) was 
established primarily to protect breeding habitat for the great green 
macaw. Approximately 43,700 ha (107,985 ac) of land identified as 
potential great green macaw breeding habitat lies within the boundaries 
of MNWR (Chun 2008, p. 113). This region was targeted because it 
contains several large nesting trees used by great green macaw breeding 
pairs. MNWR protects foraging habitat that may be critical during the 
great green macaw's breeding season. MNWR is within the larger San Juan 
La Selva (SJLS) Biological Corridor, and its goal is specifically to 
connect protected areas in southern Nicaragua to those in central Costa 
Rica (Chun 2008, p. 98). However, even in this refuge, habitat 
degradation continues to occur. A RAMSAR (the Convention on wetlands) 
report on this refuge (which is a RAMSAR site), indicated that the main 
threats there are agricultural and forestry activities, which are most 
prevalent near the Colpach[iacute] and Manat[iacute] lagoons (RAMSAR 
2012, p. 1).
    In summary, as of 2002, less than 10 percent of the great green 
macaw's original range was estimated to exist in Costa Rica (Chosset et 
al. 2002, p. 6). The great green macaw greatly depends on the almendro 
tree as its primary food and nesting resource. However, due to Costa 
Rica's complex deforestation history, the great green macaw remains 
imperiled primarily due to habitat fragmentation, degradation, and 
habitat loss. In 2004, a maximum of 35 pairs were estimated to be 
breeding in northern Costa Rica (Chosset et al. 2004, p. 32), and the 
population in this country appears to have increased since a 
conservation program and regulatory mechanisms have been in place. 
Costa Rica's population was estimated to be approximately 300 birds in 
2010 (Chassot 2010 pers. comm. in Hardman 2011, p. 11; Monge et al. 
2010, pp. 13, 22). Despite the apparent increase in the population in 
Costa Rica, the population is extremely small and has experienced 
significant decline in available habitat over the past 60 years.
Habitat Degradation
    In addition to the historical loss of habitat, the species 
continues to face threats such as habitat degradation. This species 
requires a complex suite of plant species over the course of a year for 
its nutritional needs. Pressures to its habitat such as logging, 
encroachment, habitat degradation, and likely other factors continue 
within this species' range. Despite conservation efforts in place, such 
as conservation awareness programs, research, and monitoring, the 
population has declined significantly over time and is still only 
estimated to be approximately 300 individuals. Because this species 
mates for life and has a small clutch size, the loss of any one 
individual can have a significant effect on the population. Costa Rica 
has implemented many environmental laws in conjunction with 
conservation efforts to protect species, particularly the great green 
macaw and its habitat. The situation of this species is still 
precarious, and any of the threats acting on the species, such as 
habitat loss and degradation, poaching, or other unknown factors, could 
have a significant effect on the population in Costa Rica because it is 
so small, and because of its life-history characteristics. The existing 
regulatory mechanisms, as implemented, are insufficient in Costa Rica 
to adequately ameliorate the current threats to this species.

Ecuador

    As of 2006, the Ecuadorian Government recognized 31 various legal 
categories of protected lands (e.g., national parks, biological 
reserves, geobotanical reserves, bird reserves, wildlife reserves, 
etc.). The amount of protected land (both forested and non-forested) in 
Ecuador as of 2006 was approximately 4.67 million ha (11.5 million ac) 
(ITTO 2006, p. 228). However, only 38 percent of these lands had 
appropriate conservation measures in place to be considered protected 
areas according to international standards (i.e., areas that are 
managed for scientific study or wilderness protection, for ecosystem 
protection and recreation, for conservation of specific natural 
features, or for conservation through management intervention) (ITTO 
2009, p. 1). Moreover, only 11 percent had management plans, and less 
than 1 percent (13,000 ha or 32,125 ac) had implemented those 
management plans (ITTO 2006, p. 228).
    In 2004, the Ecuadorian Minister of the Environment signed a 
ministerial decree forming the National Strategy for the In-Situ 
Conservation of the Guayaquil Macaw (Ara a. guayaquilensis) into law 
(ProForest 2005, p. 3). The strategy included the following components 
to be implemented within 10 years. Aspects of this conservation plan, 
which focuses on the Cerro Blanco Protected Forest, a stronghold for 
great green macaw, include:
     Applied investigation for the conservation of the species;
     Management of the conservation areas where the presence of 
the Guayaquil macaw has been confirmed, incorporating new areas that 
are critical for conservation of the species, and providing connecting 
corridors between the areas;
     Reforestation with appropriate tree species in its 
habitat;
     Incentives and sustainable alternatives for communities 
and private property owners within its range; and
     Conservation of the Guayaquil macaw.
    Despite the existence of this strategy, the great green macaw still 
faces significant threats in Ecuador (Horstman 2011, p. 12). There are 
likely fewer than 100 individuals of this subspecies remaining in 
Ecuador. Ecuador recognizes that threats exist to its natural heritage, 
not only to this species, but to all of its wildlife. In 2008, Ecuador 
approved Article 71 of its Constitution, which states, ``Nature has a 
right to integrally respect its existence as well as the maintenance 
and regeneration of its vital cycles, structures, functions and 
evolutionary processes.'' Article 73 also mandates, ``measures of 
precaution and restriction for all activities that could lead to the 
extinction of species, the destruction of ecosystems, or the permanent 
alteration of natural habitats.''
    Ecuador has made significant strides in conservation. Ecuador's 
Article 103 of Book IV on Biodiversity decreed that: ``It is 
prohibited, on any day or time of the year, to hunt species, whether 
birds or mammals, that constitute wildlife and that are listed in 
Appendix 1 of the present Record that are qualified as threatened or 
endangered. Hunting is likewise prohibited in certain areas or zones 
while the bans are in effect'' (Monge et al. 2009, p. 256; Unified Text 
of the Secondary Legislation of the Ministry of the Environment). 
Despite the recent advances made in conservation efforts, Ecuador has 
gone through periods of devastating habitat loss and degradation, which 
affected the great green macaw's habitat such that it only remains in 
two fragmented and small areas. It is unclear how sustainable the 
remaining habitat is, particularly because this species has specialized 
feeding requirements and requires a large range to provide its 
nutritional needs.
    The National Strategy for the In-Situ Conservation of the Guayaquil 
Macaw was revised in 2009. As a result, the first national census of 
great green macaw was conducted in Ecuador in late 2010 (Horstman 2011, 
pp. 16-17). The Cerro Blanco Protected Area has been managed by the 
Pro-Forest Foundation, an NGO, for approximately 20 years (Horstman 
2011, unpaginated).

[[Page 60015]]

Horstman indicated that, at the Cerro Blanco Reserve, the resident 
population of approximately 15 macaws travels widely outside of the 
6,475-ha (16,000-ac) reserve (http://blogs.discovery.com/animal_news/2009/11/help-for-ecuadors-great-green-macaws.html, accessed October 28, 
2011). Horstman, who has worked in this area since the early 1990s, 
indicated the need to establish a conservation corridor between Cerro 
Blanco and adjacent patches of suitable forest, and most are less than 
40.5 ha (100 ac) in size. During the past 20 years, at least 2,000 ha 
(4,942 ac) have been reforested (Monge et al. 2009, p. 9). Although 
reforestation projects have occurred, encroachment is still occurring 
(Horstman 2011, p. 12). Despite conservation efforts and regulatory 
mechanisms in place, there is still limited funding available for 
conservation efforts. Encroachment and other forms of habitat 
degradation continue to occur within its habitat (see Factor A 
discussion, above). Therefore, we find that the regulatory mechanisms 
are inadequate to ameliorate the loss and degradation of great green 
macaw habitat in Ecuador.

Honduras

    The National Conservation and Forestry Institute (ICF) (formerly 
the Protected Areas and Wildlife Department, established in 1991) is 
responsible for regulating natural resources and management of 
protected areas. The National Protected Areas System includes 17 
national parks created between 1980 and 2007. As of 2009, there were 79 
protected areas (Triana and Arce 2012, p. 1). In 1991, the Protected 
Areas and Wildlife Department (which is now the National Conservation 
and Forestry Institute (ICF)) was designated to manage natural 
resources and protected areas (Devenish et al. 2009, p. 257; Decree no. 
74-91, 1991). Prior to 1991, wildlife was managed by the Honduran 
Department of Wildlife and Ecology (RENARE).
    Decree 98-2007, the Forest Law of Honduras, repealed Decree 163-93 
of 1993, which contained the Law on Incentives for Forestation, 
Reforestation, and Forest Protection. The Forest Law sets forth the 
purposes of the law, and regulates the use of forestry areas, the 
rational and sustainable management of forestry resources, protected 
areas, and wildlife. The law contains definitions and created a series 
of administrative agencies charged with the implementation of forestry 
regulations, including the National Forestry Consultative Council. This 
law also formed the National Forestry Research System and the National 
Institute for Forestry Conservation and Development (211 provisions; 
pp. 1-17).
    Before the 2007 Forest Law was approved, at least 38 laws governed 
the sector, creating a confusing policy framework. The situation is 
further complicated because, in many cases, forest tenure (ownership, 
tenancy, and other arrangements for the use of forests) is unclear. 
Although most forest is officially state-owned (FAO 2007), states have 
little practical authority over forest management, and individuals 
exercise de facto ownership. Corruption is a barrier to legal logging 
because it facilitates illegal operations and creates obstacles to 
legal ones (Pellegrini 2011, p. 18; Rodas et al. 2005, p. 53). Bribes 
are extorted from certified community forestry operations, and, 
reportedly, without bribes, transport of legal wood becomes impossible 
(Pellegrini 2011, p. 18; Rodas et al., 2005, p. 53).
    The new 2007 Forest Law was supported by environmental groups, but 
its implementation was delayed. The law included the abolition of the 
Honduran Forest Development Corporation (COHDEFOR) (which received 
unanimous support), more resources for enforcement, and harsher 
penalties against those who commit forest-related crimes. Previously, 
the director of COHDEFOR and other political leaders were owners or 
employees of logging companies, an apparent conflict of interest 
(Pellegrini 2011, p. 20). Also at that time, the army was involved in 
enforcement. Out of the resources that were spent for the forestry 
sector, the military absorbed 70 percent without producing any evidence 
that enforcement had improved (Pellegrini 2011, p. 20).
    Currently in Honduras, the great green macaw is believed to exist 
in eastern Honduras in suitable habitat distributed from Olancho to the 
R[iacute]o Pl[aacute]tano Biological Reserve, the Tawahka Biological 
Reserve, and Patuca National Park (Monge et al. 2009, p. 39). Its range 
encompasses both unprotected and protected areas; however, timber 
exploitation occurs even in areas designated as protected. This 
practice has created conflicts in protected areas such as the 
R[iacute]o Pl[aacute]tano Biosphere Reserve, an area that is considered 
critical for its conservation (Lopez and Jim[eacute]nez 2007, p. 26). 
Demand for mahogany, which has been one of the most extracted species 
in the area (Lopez and Jim[eacute]nez 2007, p. 26), has also put 
pressure on this species' habitat. Selective logging creates openings 
in forest canopies and changes the ecosystem dynamics and composition 
of plant species. Income from logging is higher than that earned for 
crops and cattle, making logging far more lucrative for locals. 
However, after areas are logged, they become more accessible and are 
then often converted to uses such as crops and cattle grazing.
    Indigenous communities have rights to use many protected areas. 
Article 107 of the Honduran Constitution protects the land rights of 
indigenous people. It is the duty of the government to create measures 
to protect the rights and interests of indigenous communities in the 
country, especially with respect to the land and forests where they are 
settled (Article 346). As an example of land use by Honduran indigenous 
communities, between 15 and 40 percent of the total value of 
consumption for two indigenous Tawahka communities was found to be 
derived directly from the forest (Godoy et al. 2002, p. 404). Struggle 
over land rights is a difficult issue for indigenous communities in 
Honduras. Logging and mining are some of the biggest threats not only 
to the great green macaw, but also to the indigenous communities. 
Indigenous cultures generally have a low impact on the forests (Stocks 
et al. 2007, pp. 1,502-1,503). Because indigenous communities want 
their lands protected for their traditional way of life, NGOs are 
working with these communities to protect reserves in Honduras, which 
should ultimately benefit the great green macaw.
    In 1996, the R[iacute]o Pl[aacute]tano Biosphere Reserve was placed 
on the ``World Heritage Site in Danger'' list, but it was removed from 
the list in 2007, due to a significant improvement in conservation 
efforts by NGOs. Several NGOs are working in this area including the 
Mosquitia Paquisa (MOPAWI) and the Rio Pl[aacute]tano Biosphere Project 
(UNEP-WCMC 2011, p. 5). However, investigations in 2010 and 2011 
indicate that there are still problems within the reserve (UNESCO 2011, 
pp. 1-3). UNESCO, as recently as 2011, conducted a survey in the 
R[iacute]o Pl[aacute]tano Reserve and found illegal activity within the 
core zone (UNESCO 2011, pp. 1-3). Clearing of land for cattle grazing 
and illegal fishing and hunting along the river is ongoing. The area is 
protected by policy by the Department of Protected Areas and Wildlife, 
State Forestry Administration in Honduras. The reserve management plan, 
implemented in 2000, included zoning and specific plans for 
conservation issues. One of the goals of the reserve's conservation 
plan is to integrate local inhabitants with their environment in part 
via sustainable agricultural practices. This practice has been found to 
be a good tool in forest conservation (Pellegrini 2011, pp. 3-8). The 
reserve

[[Page 60016]]

plan established buffer zones, cultural zones, and nucleus zones. 
Indigenous communities living in the reserve and buffer zone are 
allowed to use the resources within the reserve. The integration of 
indigenous populations plays a large part in the success of the 
conservation plan, both inside the reserve and outside the reserve in 
the buffer and peripheral zones (Pellegrini 2011, p. 3; Stocks et al. 
2007, pp. 1502-1503). This reserve also receives some funding from the 
World Wildlife Fund and other private organizations that assist in the 
management of the reserve. However, there are currently no park guards 
or any official entity actively patrolling or guarding the reserve to 
enforce restrictions.
    There is a complex history concerning the balance of land rights of 
indigenous communities and preservation of habitat for species such as 
the great green macaw. In Honduras, there is a gap between forestry 
policy objectives and the state of forestry. The policy frameworks 
exist to manage timber extraction, but tools are not implemented 
(Pellegrini 2011, p. 1). COHDEFOR had been responsible for forestry 
development and enforcement of laws. The Honduran Government began to 
decentralize COHDEFOR beginning in 1985 (Butler 2012, unpaginated) due 
to its ineffectiveness. As of 2001, the management of Honduran forests 
was administered by the Administraci[oacute]n Forestal del Estado (AFE, 
Government Forestry Administration), Corporaci[oacute]n 
Hondure[ntilde]a de Desarrollo Forestal (COHEFOR Honduran Forestry 
Development Corporation) (Moreno and Marineros 2001, p. 2). Land use 
planning occurs at the national level; however, identifying the best 
use of areas has not been implemented (Pellegrini 2011, p. 17). In 
addition, estimates of illegal logging are approximately 80 percent of 
the total volume extracted for broadleaf and 50 percent for coniferous 
species (Richards et al. 2003, p. 1).
    Honduras is making progress in managing its forested resources. In 
2010, Honduras implemented Agreement number 011-2010 (Ecolex 2011), the 
Forestry Reinvestment Fund and Plantation Development, and its goal is 
to recover areas of degraded or denuded forests. In 2010, Honduras also 
put into place Decision No. 31/10, the General Regulation of Forestry 
Law, Protected Areas and Wildlife (Ecolex 2011). This covers the 
administration and management of forest resources, protected areas, and 
wildlife. Despite the progress made in Honduras with respect to laws 
and regulatory mechanisms that affect the great green macaw and other 
wildlife, the species continues to face habitat loss and degradation in 
Honduras.

Nicaragua

    Nicaragua's General Environmental and Natural Resources Law No. 
217, issued in 1996, is considered the legal framework that defines the 
standards and mechanisms in regard to the use, conservation, 
protection, and restoration of the environment and natural resources in 
a sustainable manner. It recognizes the sustainable development 
concept. By 2004, Nicaragua had enacted 10 environmental laws and was a 
member of regional and international environmental agreements (Moreno 
2004, p. 9). As of 2004, Nicaragua was moving towards the consolidation 
of a National System of Protected Areas (SINAP) in order to preserve 
the country's biological wealth (Moreno 2004, p. 9). SINAP consists of 
National Protected Areas, Municipal Ecological Parks, and Private 
Wildlife Reserves of ``ecological and social relevance at the local, 
national, and international level, defined in conformance with the law, 
and designated according to management categories that permit 
compliance with national policies and objectives of conservation'' 
(McGinley 2009, p. 19; Protected Areas Regulations: Article 3). 
However, the overall protection and administration of SINAP is hindered 
by an inability to administer its financial and human resources 
(McGinley 2009, p. 20). Of the 72 national protected areas, only 23 had 
approved management plans in 2008, another 19 were in some phase of the 
approval process, and 30 protected areas had no management plan at all 
(McGinley 2009, p. 20). Despite protections in place, enforcement has 
been lacking in protected areas, and poverty continues to be a huge 
concern in Nicaragua (FAO 2011, pp. 1-2; McGinley et al. 2009, p. 16).
    Three assessments of the effectiveness of Nicaragua's laws and 
regulations with respect to wildlife and forestry laws were recently 
conducted (Pellegrini 2011; McGinley et al. 2009; Castell[oacute]n et 
al. 2008). The first explored the relationship between forest 
management and poverty (Pellegrini 2011). The research published in 
2009 evaluated Nicaragua's Tropical Forests and Biological Diversity 
(McGinley et al. 2009, entire). The other report evaluated the 
effectiveness of Nicaragua's wildlife trade policies 
(Castell[oacute]n.et al. 2008, entire). In Nicaragua, the organization 
responsible for regulation and control of the forestry sector is the 
National Forest Institute (INAFOR), which is under the Ministry of 
Agriculture, Livestock and Forestry (MAGFOR). The other relevant 
ministry is the Nicaraguan Ministry of Environment and National 
Resources (MARENA), which supports conservation awareness programs for 
this species. In early 2003, MARENA created the Municipal Environmental 
Unit in order to decentralize environmental functions. Although a good 
legal framework exists in Nicaragua to protect its natural resources, 
there are still on-the-ground problems that affect this species. For 
example, in the Indio-Ma[iacute]z Biological Reserve, one of the 
strongholds for this species, each forest guard in the control posts 
along the border of the reserve is responsible for monitoring a stretch 
of 8 km (5 mi) of the border and an area of 70 km\2\ (27 mi\2\) (Rocha 
2012, pp. 3-6; Ravnborg et al. 2006, p. 6). There are communication and 
perception problems that are prevalent within the reserve that 
perpetuate the inability to adequately manage the resources within the 
reserve. These resources are used both legally and illegally by Costa 
Ricans who cross the San Juan River and the local communities who live 
in Nicaragua (Rocha 2012, pp. 3-6).
    In 2008, the Government of Nicaragua published a report on the 
status of its wildlife laws and mechanisms (Castellon et al. 2008, 
entire). It reported the following findings (p. 9):
     Nicaragua's current laws are inadequate to protect and 
sustain domestic and international trade in CITES species. They are 
unfocused and lack provisions on habitat degradation and biological 
productivity.
     Nicaragua does not have a written wildlife trade policy or 
laws to underpin sustainable species management in domestic and 
international trade. The regulatory instruments pertaining to 
sustainable management of wildlife trade are relevant and coherent and 
provide a basis for the formulation of such a policy.
     The nonregulatory instruments for measuring the commercial 
sustainability of wildlife trade are rarely used. The most important of 
them are: monitoring, research, education, and information.
     Study of wildlife harvesting shows that the income from 
trade in harvested species goes principally to external actors, with 
little or no benefit to rural communities or populations.
    The 2008 study also reported that the Government of Nicaragua was 
unable to find a single case in which the application of its laws led 
to actual fines or penalties for harvesting or trading banned species 
(McGinley 2009, p. 22). It found that nonregulatory instruments

[[Page 60017]]

such as monitoring, research, education, and information are poorly 
used in the oversight of commercial wildlife trade in Nicaragua 
(McGinley 2009, p. 22). Despite these findings, a review undertaken by 
the CITES Secretariat found that the legislation of Nicaragua has been 
determined to be sufficient to properly implement the CITES Treaty (see 
discussion below). The country has made an effort to protect its 
resources and is attempting to address the management of its natural 
resources.
    In addition, specific, targeted conservation measures are 
occurring. An NGO in Nicaragua, with the support of MARENA, is 
promoting conservation of this species. They have initiated a campaign 
to educate communities in part by posting messages on buses on three 
highly traveled public routes in Managua. For example, one message 
describes why buying endangered species as pets is not a good idea; 
rather, they should remain in the wild. Additionally, in 2003, 
Nicaragua and Costa Rica participated in the First Mesoamerican 
Congress for Protected Areas. Senior representatives of both countries 
discussed ways to explore the framework of connectivity between 
protected areas (Villate et al. 2008, p. 52). As a result, several 
active conservation measures for the great green macaw in Nicaragua are 
under way, such as the development of connected habitat corridors, and 
the great green macaw conservation workshop was held in 2008. In 
Nicaragua's Indio-Ma[iacute]z Biological Reserve, training measures for 
monitoring the great green macaw have been implemented. For example, 
technicians associated with Fundacion del Rio have been trained in 
great green macaw research (Chassot et al. 2006, p. 86). The species' 
population is estimated to be only 871 individuals in Nicaragua and 
Costa Rica combined (Monge et al. 2010, p. 21), and pressures continue 
to occur to the species and its habitat. Despite regulatory mechanisms 
in place and the existence of many strategies in Nicaragua to combat 
threats to the species such as deforestation, habitat loss, and 
poaching for the wildlife trade, these activities continue.
    The impoverished rely strongly on forest products (Pellegrini 2011, 
pp. 21-22). In an attempt to reduce poverty and at the same time 
conserve forested areas, analyses addressing poverty reduction were 
conducted prior to 2002. Strategies, described as Poverty Reduction 
Strategy Papers (PRSPs), recommended approving a forestry law by 2002 
(which actually was approved at the end of 2003) and addressing 
deforestation as a source of ecological vulnerability. As part of its 
poverty reduction strategy, Nicaragua developed a National Development 
Plan (Government of Nicaragua 2005 in Pellegrini 2011, pp. 21-22), the 
goal of which was to strengthen the whole forestry production chain. 
However, the plan was reported not to have been effectively implemented 
(Pellegrini 2011, p. 22). The main policy instruments that set the 
framework for forestry were the Forest Law and the logging ban. The 
Forest Law establishes the system of forest management (Pellegrini 
2011, pp. 21-22). The law includes incentives for sustainable 
practices; however, Pellegrini noted that it is virtually impossible to 
take advantage of the law's provisions without support by external 
organizations such as NGOs (Pellegrini 2011, p. 22; TNC 2007, pp. 3-7).
    Nicaragua is focusing efforts on the restoration and protection of 
forested areas, and its goal was to reduce the deforestation rate from 
70,000 ha (172,974 ac) to 20,000 ha (49,421 ac) per year by 2010 
(McGinley 2009, p. 28). Recently, the Associated Foresters of Nicaragua 
(FORESTAN), in cooperation with a local NGO, the Instituto de 
Investigaciones y Gesti[oacute]n Social (INGES), began an initiative to 
increase forest cover. Their goal is to incorporate conservation and 
production areas over 5,000 ha (12,355 ac), and more effectively use 
commercially valuable tree species while at the same time creating 
permanent jobs (INGES-FORESTAN 2005 in Sinreich 2009, p. 63). In 2006, 
a logging ban was put in place. The ban prohibited extraction of six 
species of wood and any logging operation in protected areas or within 
15 km (9 mi) of all national borders, and it put the army in charge of 
enforcement (Government of Nicaragua 2006 in Pellegrini 2011, p. 23). 
However, deforestation rates may have increased even after the ban's 
approval (Guzm[aacute]n 2007, pp. 1-2). Although Nicaragua attempts to 
manage its natural resources, it has a large challenge due to the 
pressures for its forest resources in combination with extreme poverty 
(FAO 2011, p. 1; McGinley et al. 2009, p. 11). Despite these efforts, 
pressure on the great green macaw's habitat continues.

Panama

    In Panama, the great green macaw's stronghold is believed to be in 
Dari[eacute]n National Park, which borders Colombia (Monge et al. 2009, 
p. 68; Angehr in litt. 1996 in Snyder et al. 2000, pp. 121-123; Ridgley 
1982). The Dari[eacute]n region encompasses nearly 809,371 ha (2 
million ac) of protected areas, including Dari[eacute]n National Park 
and Biosphere Reserve, Punta Pati[ntilde]o Natural Reserve, Brage 
Biological Corridor, and two reserves for indigenous communities (TNC 
2011, p. 1). Panama's National System of Protected Areas (SINAP) is 
managed by the National Environmental Authority (ANAM) and consists of 
66 areas, totaling 2.5 million ha (6.18 million ac) (Devenish et al. 
2009b, pp. 1-2). Of these, 19 have management plans, and 36 have been 
through a process of strategic planning (ANAM 2006, unpaginated).
    ANAM was established in 1998, through the General Environmental Law 
of Panama (Law 41). ANAM is the primary government institution for 
forest and biodiversity conservation and management. ANAM plans, 
coordinates, regulates, and promotes policies and actions to use, 
conserve, and develop renewable resources of the country. Its mission 
statement is to guarantee a healthy environment through the promotion 
of rational use of natural resources, the organization of environmental 
management, and the transformation of Panamanian culture to improve the 
quality of life (Virviescas et al. 1998, p. 2). Law 41 also provides 
the framework for SINAP. Environmental protection in Panama falls under 
the jurisdiction of three government agencies, the Institute for 
Renewable Natural Resources, the Ministry of Agricultural Development, 
and the Ministry of Health. There are 17 management categories of 
protected areas that were established through INRENARE's Resolution 09-
94. A later law, the Forest Law of 2004, established protections for 
three types of forest, which covers 36 percent of the country.
    There are political and economic pressures to develop many areas 
(Devenish et al. 2009b, p. 291). Deforestation, in addition to the lack 
of management, and lease periods for these concessions of 2 to 5 years, 
have left only an estimated 250,000 to 350,000 ha (617,763 to 864,868 
ac) of production forests in Panama (Gutierrez 2001a in Parker et al. 
2004, p. I-10). Additionally, many protected areas in Panama lack 
adequate staff and resources to patrol the areas or enforce regulations 
(Devenish et al. 2009b, p. 291). In 1986, Panama initiated a national 
forest strategy (Plan de Acci[oacute]n Forestal de Panama or PAFPAN) 
supported by FAO; however the plan reportedly did not directly tackle 
the causes of deforestation. Between 1980 and 1990, concessions for 
77,800 ha (192,248 ac) of production forests were awarded to 23 
companies, for periods ranging from 2 to 5 years (Parker et al. 2004, 
p. II-4). In 1994, a new forestry law was approved, which

[[Page 60018]]

institutionalized forest management. Now, concessions exist only in the 
Dari[eacute]n Province (Parker et al. 2004, p. II-4). Between 1992 and 
2000, the Dari[eacute]n Province was one of Panama's provinces that 
experienced the greatest declines (11.5 percent) in forest cover 
(Parker et al. 2004, p. 32). However, there are activities in place to 
combat these pressures. For example, a training program exists to 
increase capacity in issues such as planning, geographic information 
systems, sustainable tourism, trail construction and management for 
park staff, community groups, and other stakeholders in the protected 
area system.
Dari[eacute]n National Park
    Dari[eacute]n National Park extends along about 80 percent of the 
Panama-Colombia border and includes part of the Pacific coast. The area 
has been under protection since 1972, with the establishment of Alto 
Dari[eacute]n Protection Forest. It was declared a national park in 
1980. The park is zoned as a strictly protected core zone of over 
83,000 ha (205,097 ac). Another zone consists of 180,000 ha (444,789 
ac) and contains indigenous Indian populations that have maintained 
their traditional way of life and culture. Approximately 8,000 ha 
(19,768 ac) is designated for tourism and environmental education, and 
the last zone is described as an ``inspection zone'' which is 40-km 
(25-mi) wide, and spans the Panama-Colombia border. The Dari[eacute]n 
forests are threatened from logging, agriculture expansion, burning, 
and hunting and gathering (TNC 2011, pp. 1-2; Monge et al. 2009, p. 
68). Other threats to forest in the region include the development of 
projects such as dams and highways (Parker et al. 2004, pp. II-7-II-8).
    Since 1986, the Asociaci[oacute]n Nacional para la Conservacion de 
la Naturaleza (ANCON) has been actively involved in conservation of the 
park in conjunction with INRENARE, the World Wildlife Fund, and other 
conservation entities. In 1995, a biodiversity conservation project was 
initiated. The project's goal was to involve local communities in 
conservation and sustainable use activities, and was funded by the 
United Nations Environment Programme (UNEP) and the Global Environment 
Facility. The Nature Conservancy (TNC) is also active in conservation 
efforts in this area through its Parks in Peril program (TNC 2011, pp. 
1-2).
    Panama has also initiated reforestation efforts. For example, 
beginning in the 1960s, Panama began to plant Pinus caribaea (pine 
species) in degraded areas of the Cordillera of the central region. 
Additionally, in 1992, a law was passed to provide incentives for the 
establishment of plantations; however, these were mainly exotic species 
(Parker et al. 2004, p. III-6). Panama is now implementing 
reforestation and timber production projects that focus on native 
species. This initiative is known as the ``Native Species Reforestation 
Project'' (Proyecto de Reforestaci[oacute]n con Especies Nativas; 
PRORENA) (Schmidt 2009, p. 10). Forestry managers have realized that, 
in some cases, native species are better adapted and perform better 
than introduced species. Since 2001, the joint Native Species 
Reforestation Project between the Smithsonian Tropical Research 
Institute and the Yale School of Forestry has conducted ongoing 
research on trees native to Panama. The almendro tree, which is vital 
to the great green macaw's habitat, has been the subject of research 
projects in Panama because of its high commercial value (Schmidt 2009, 
p. 17). Despite efforts to reduce deforestation activities, management 
problems remain. A study conducted in 2004 suggested that the Forestry 
Department needs increased autonomy, funding, and staff, and a more 
appropriate mandate (Parker et al. 2004, pp. 10-11). The study 
suggested that strengthening the Parks and Wildlife Service through 
increased staffing and resources would enable them to protect and 
manage protected areas (Parker et al. 2004, pp. 10-11).
    In summary, Panama has a suite of environmental laws in place, and 
conservation measures are being implemented by the government in 
collaboration with some NGOs. However, there is very little information 
available about the great green macaw in Panama (Monge et al. 2009, p. 
68), and the information indicates that this species continues to face 
pressures to its habitat. Despite Panama's participation in 
conservation initiatives and Panama's regulatory mechanisms in place, 
there are still significant pressures for resources in the great green 
macaw's habitat.

International Wildlife Trade (CITES)

    The CITES Treaty requires Parties to have adequate legislation in 
place for its implementation. A complete discussion on CITES is found 
under Factor D for the military macaw. Within the recent past (since 
2000), 261 live great green macaws were reported to have been imported 
by CITES reporting countries, and none of these live specimens were 
reported as wild origin (UNEP-WCMC CITES Trade Database, accessed 
December 8, 2011). Under CITES Resolution Conference 8.4 (Rev. CoP15), 
and related decisions of the Conference of the Parties, the National 
Legislation Project evaluates whether Parties have adequate domestic 
legislation to successfully implement the Treaty (CITES 2011a). In 
reviewing a country's national legislation, the CITES Secretariat 
evaluates factors such as whether or not a Party:
     Has domestic laws that prohibit trade contrary to the 
requirements of the Convention;
     Has penalty provisions in place for illegal trade, and has 
designated the responsible Scientific and Management Authorities; and
     Provides for seizure of specimens that are illegally 
traded or possessed.
    The CITES Secretariat determined that the legislations of Colombia, 
Costa Rica, Honduras, Nicaragua, and Panama are sufficient to properly 
implement the Treaty (http://www.cites.org, SC58 Doc. 18 Annex 1, p. 
1). These governments were determined to be in Category 1, which means 
they meet all the requirements to implement CITES. Ecuador was 
determined to be in Category 2, with a draft plan, but not enacted 
(http://www.cites.org, SC59 Document 11, Annex p. 1, accessed December 
16, 2011). This means the CITES Secretariat determined that the 
legislation of Ecuador meets some, but not all, of the requirements for 
implementing CITES. Based on the limited amount of reported 
international trade for this species, particularly in wild-caught 
specimens, the range countries, including Ecuador, have effectively 
controlled legal international trade of this species. Therefore, we 
find CITES is an adequate regulatory mechanism.

Summary of Factor D

    In the range countries for this species, we recognize that 
conservation activities are occurring, and each country has enacted 
laws with the intent of protecting its species and habitat. For 
example, in 2002, the San Juan--La Selva Biological Corridor, an area 
of 60,000 ha (148,263 ac), was implemented to protect the nesting 
places and migration flyway of the great green macaw in Costa Rica, as 
far as the Nicaragua border, where very little is known about the 
species. However, most of the suitable habitat is restricted to 
protected areas in clustered locations. Oliveira et al. (2007) found 
that forests in conservation units were four times better at protecting 
against deforestation than unprotected areas (Oliveira et al. 2007, p. 
1,235). Despite regulatory mechanisms established by this species' 
range countries and despite the species' existence in areas designated 
as protected, this species has experienced

[[Page 60019]]

threats such that its populations are now so small that any pressure 
has a more significant effect. Parks, without management, are often 
insufficient to adequately protect the species.
    The information available with respect to the species' population 
numbers is extremely limited in its range countries, and the 
populations of this species in these countries all likely range from a 
few individuals to a few hundred individuals (Botero-Delgadillo and 
P[aacute]ez 2011, p. 91; Monge et al. 2010, p. 22; Monge et al. 2009, 
p. 256). The populations are all in relatively disconnected areas. Its 
suitable habitat has been severely constricted due to deforestation. In 
all of the range countries, there is clear evidence of threats to this 
species due to activities such as habitat destruction and degradation, 
and poaching, and there is decreased viability due to small population 
sizes, despite the laws and regulatory mechanisms in place. Given that 
the species' habitat continues to be fragmented and degraded, it is 
unlikely that any conservation measures are adequately mitigating the 
factors currently acting on the species.
    Based on the best available information, despite protections in 
place by the respective governments, we find that the existing 
regulatory mechanisms are either inadequate or inadequately enforced to 
protect the species or to mitigate ongoing habitat loss and 
degradation, poaching, and severe population declines. Habitat 
conservation measures within these range countries do not appear to be 
sufficient to adequately mitigate future habitat losses. This is due to 
a suite of factors, such as high rates of poverty in the range of the 
great green macaw and subsequent pressures for resources, and 
conflicting management goals (such as economic development and 
protection of its resources) of its range countries. Therefore, we find 
that the existing regulatory mechanisms are inadequate to mitigate the 
current threats to the continued existence of the great green macaw 
throughout its range.

E. Other Natural or Manmade Factors Affecting Its Continued Existence

Small Population Size and Stochastic Events

    There have been few quantitative studies of great green macaw 
populations (Botero-Delgadillo and P[aacute]ez 2011, p. 91; Monge et 
al. 2010, p. 12; Monge et al. 2009.). In 2009, the combined estimate 
for Costa Rica and Nicaragua was 871 individuals (Monge et al. 2010, p. 
21), and the estimate for Ecuador was fewer than 100 (Horstman 2011, p. 
17). There are no current population estimates for Panama, Honduras, 
and Colombia, but the global population is believed to be fewer than 
3,700 individuals (Monge et al. 2009, pp. 68, 79, 213). Small, 
declining populations can be especially vulnerable to environmental 
disturbances such as habitat loss (Harris and Pimm 2008, pp. 163-164; 
O'Grady 2004, pp. 513-514; Brooks et al. 1999, pp. 1,146-1,147). In 
Costa Rica, the great green macaw has been eliminated from 
approximately 90 percent of its former range, and one estimate 
indicated that there were only 275 birds remaining in 2010 (Chassot 
2010 pers. comm. in Hardman 2011, p. 11). Isolated populations are more 
likely to decline than those that are not isolated (Davies et al. 2000, 
p. 1,456), as evidenced by the Ecuadorian population. Additionally, the 
great green macaw's restricted range, combined with its small 
population size and low prospect for dispersal (Chosset et al. 2004, p. 
32), makes the species particularly vulnerable to the threat of any 
adverse natural (e.g., genetic, demographic, or stochastic) and manmade 
(e.g., habitat alteration and destruction) events that could destroy 
individuals and their habitats.
    The government of Costa Rica, in cooperation with Zoo Ave Wildlife 
Conservation Park, located in Garita de Alajuela, has participated in a 
captive bird breeding program (Herrero 2006, pp. 2-3) since 1994. Some 
of the birds produced have been released in protected areas. However, 
captive breeding is a controversial issue, mainly due to the 
reintroduction of individuals. One of the concerns is that the 
reintroduced birds introduce infectious diseases (which may be in 
dormant phase for a period of time) into the wild (Brightsmith et al. 
2006 in Herrero 2006, pp. 2-3).
    There are multiple features of this species' biology and life 
history that affect its ability to respond to habitat loss and 
alteration, as well as to stochastic environmental events. Due to its 
current restricted distribution and habitat requirements, stochastic 
events could further isolate individuals. An example of a stochastic 
event impacting the species occurred in 2010, and the death of several 
nestlings was recorded (Chosset and Arias 2010, p. 15). One nestling 
fell out of a tree, and, in another case, a branch fell on a nestling 
while it was actually in the nest and it died (Chosset and Arias 2010, 
p. 15). Losses such as these can have a significant effect on the 
population. Additionally, limited available suitable habitat makes it 
difficult for the species to recolonize isolated habitat patches, which 
presently exist in a highly fragmented state. This, in combination with 
the species' nutritional needs, results in the species requiring large 
home ranges.

Border Conflict

    One of the difficulties in the conservation of this species that 
may not be readily apparent is border conflict. For example, at the 
border of Nicaragua and Costa Rica, despite cooperation efforts; 
conflict continues (U.S. Department of State 2012, unpaginated; Berrios 
2004, entire). The Nicaraguan-Costa Rican border is one of the most 
conflict-heavy frontiers in Central America (Lopez and Jimenez 2007, p. 
21). Migration issues, navigation rights in border rivers, border 
delineation, and cultural differences all affect these countries' 
relations (Lopez and Jimenez 2007, p. 21). Additionally, this area has 
historically experienced exploitation of its natural resources. Since 
the beginning of last century, foreign companies have engaged in 
logging, rubber extraction, and mining (Lopez and Jimenez 2007, pp. 24-
25). After these resources were depleted and these activities were no 
longer profitable, some companies left, leaving behind harmful 
environmental impacts (Lopez and Jimenez 2007, pp. 24-25). These 
activities have resulted in polluted rivers, high levels of 
sedimentation in coastal lagoons, and deforested areas (Lopez and 
Jimenez 2007, pp. 24-25). These activities all subsequently affect the 
habitat of the great green macaw.
    Deforestation in Nicaragua has a complex history. After a civil war 
throughout the 1980s, land tenure policies inadvertently encouraged 
farming techniques that led to deforestation, soil erosion, and general 
land degradation (Sinreich 2009, p. 11). Later, during the 1990s, 
COHDEFOR opened up timber extraction opportunities to local community 
organizations, mainly cooperatives, to help mitigate the economic 
situation for local people. Licenses allowed the use of fallen wood and 
timber extraction for sale at local markets. However, a study conducted 
between 1998 and 2000 found that local groups had extracted an enormous 
amount of timber and there was no monitoring (Col[iacute]ndres and 
Rub[iacute] 2002). Although the government offered support to 
communities in its border regions during the period of 1994-1999, 
tensions continue to affect the Bosawas region of Nicaragua, one of the 
areas believed to contain a great green macaw population (Lopez and 
Jim[eacute]nez 2007, p. 26). Land rights disputes continue to

[[Page 60020]]

occur in Bosawas, and land use rights are often unclear. Although the 
Government of Nicaragua is attempting to manage these issues 
(Pellegrini 2011, p. 21), conflict and practices that degrade the great 
green macaw's habitat persist both in the Bosawas Reserve and the 
Indio-Ma[iacute]z Biological Reserve.

Climate Change

    Our analysis under the ESA includes consideration of ongoing and 
projected changes in climate (see discussion under the military macaw). 
The 2008 workshop in Costa Rica addressed environmental disasters in 
the evaluation and assessment of the great green macaw, although 
climate change was not specifically addressed. Researchers describe 
environmental disasters as events that occur infrequently but that can 
drastically affect reproduction or survival. Monge et al. reported that 
in Costa Rica, the number of active nests in 2000 was well below the 
average of other years. The researchers linked this with the strong El 
Ni[ntilde]o event that occurred during 1997-1998 (Monge et al. 2009, p. 
149). The researchers stated that in the last 50 years there were two 
major El Ni[ntilde]o events, and, therefore, one would expect that in 
100 years there would be four events of this nature, which could 
subsequently reduce reproduction by 30 percent (Monge et al. 2009, p. 
149). However, this correlation between the low number of active nests 
and the El Ni[ntilde]o event is not strongly supported, nor do we have 
supporting evidence that this is directly related to climate change. We 
are not aware of any information that indicates that climate change 
threatens the continued existence of the great green macaw.

Summary of Factor E

    A species may be affected by more than one threat. Impacts 
typically operate synergistically, and are particularly evident when 
small populations of a species are decreasing. Initial effects of one 
threat factor can exacerbate the effects of other threat factors 
(Laurance and Useche 2009, p. 1,432; Gilpin and Soul[eacute] 1986, pp. 
25-26). Further fragmentation of populations can decrease the fitness 
and reproductive potential of the species, which can exacerbate other 
threats. Lack of a sufficient number of individuals in a local area or 
a decline in their individual or collective fitness may cause a decline 
in the population size, even with suitable habitat patches. Within the 
preceding review of the five factors, we have identified multiple 
threats that have interrelated impacts on this species. Thus, the 
species' productivity may be reduced because of any of these threats, 
either singularly or in combination. These threats occur at a 
sufficient scale such that they are affecting the status of the species 
now and in the future.
    This species' current range is highly restricted and severely 
fragmented. Each breeding pair requires a large home range to meet its 
nutritional requirements; it is a large macaw, and its sources of food 
are becoming scarcer and farther apart, which requires more energy 
consumption to locate. The susceptibility to extirpation of limited-
range species can occur for a variety of reasons, such as when a 
species' remaining population is already too small or its distribution 
too fragmented such that it may no longer be demographically or 
genetically viable. The species' small and declining population size, 
reproductive and life-history traits, and highly restricted and 
severely fragmented range together increase the species' vulnerability 
to any other stressors. Based on the above evaluation, we conclude that 
the effects of isolation and its small, declining population size, 
combined with the threats of continued fragmentation and isolation of 
suitable forest habitats, pose a threat to the great green macaw.

Finding and Status Determination for the Great Green Macaw

    Although precise quantitative estimates are not available, the best 
available information suggests that populations of great green macaws 
have substantially declined, and this species likely persists at 
greatly reduced numbers relative to its historical abundance. The 
factors that threaten the survival of the great green macaw are: (A) 
Habitat destruction, fragmentation, and degradation; (B) 
Overutilization via poaching; (D) inadequacy of regulatory mechanisms 
to reduce the threats to the species; and (E) small population size and 
isolation of remaining populations.
    The direct loss of habitat through widespread deforestation and 
conversion of primary forests to human settlement and agricultural uses 
has led to the fragmentation of habitat throughout the range of the 
great green macaw and isolation of the remaining populations. The 
species has been locally extirpated in many areas and has experienced a 
significant reduction of suitable habitat. The current suitable habitat 
in Costa Rica is now less than 10 percent of its original suitable 
habitat (Chosset et al. 2004, p. 38). This species exists generally in 
small and fragmented populations, and in many cases, the population is 
so small that intense monitoring and management of the population is 
under way. The San Juan-La Selva Biological Corridor was established to 
connect forest patches and join 20 protected areas (Chosset and Arias 
2010, p. 5) specifically to preserve habitat for this species.
    We have very little information about the species in many parts of 
its range (Botero-Delgadillo and P[aacute]ez 2011, p. 91; Monge et al. 
2009, p. 68). In 2008, experts from this species' range countries 
attended a conference to evaluate the viability of its populations and 
its habitat (Monge et al. 2009, entire). In general, they concluded 
that populations are viable but they still face threats. The workshop 
also addressed goals for the conservation of the species; in some parts 
of its range, conservation efforts are intensive. Based on our review 
of the best available scientific and commercial information pertaining 
to the five factors, the threats to the species are generally 
consistent throughout its range. In many of the range countries, its 
populations are very small, and specific information about the status 
of the species is not available in all countries. However, habitat loss 
and degradation is prevalent throughout this species' range; its 
suitable habitat has severely contracted, and habitat loss is likely to 
continue into the future due to pressures for resources. Poaching is 
known to occur within many parts, if not all parts, of its range. 
Despite conservation awareness programs, poverty is prevalent within 
the range of the species, and the species is quite valuable 
commercially, so poaching continues to occur. We do not find that the 
effects of current threats acting on the species are being ameliorated 
by regulatory mechanisms. Therefore, we find that listing the great 
green macaw as endangered is warranted throughout its range, and we 
propose to list the great green macaw as endangered under the ESA.

Available Conservation Measures

    Conservation measures provided to species listed as endangered or 
threatened under the ESA include recognition, requirements for Federal 
protection, and prohibitions against certain practices. Recognition 
through listing results in public awareness, and encourages and results 
in conservation actions by Federal and State governments, private 
agencies and interest groups, and individuals.
    The ESA and its implementing regulations set forth a series of 
general prohibitions and exceptions that apply to all endangered and 
threatened wildlife. These prohibitions, at 50 CFR 17.21 and 17.31, in 
part, make it illegal for any person subject to the jurisdiction

[[Page 60021]]

of the United States to ``take'' (includes harass, harm, pursue, hunt, 
shoot, wound, kill, trap, capture, or to attempt any of these) within 
the United States or upon the high seas; import or export; deliver, 
receive, carry, transport, or ship in interstate commerce in the course 
of commercial activity; or sell or offer for sale in interstate or 
foreign commerce any endangered wildlife species. It also is illegal to 
possess, sell, deliver, carry, transport, or ship any such wildlife 
that has been taken in violation of the ESA. Certain exceptions apply 
to agents of the Service and State conservation agencies.
    Permits may be issued to carry out otherwise prohibited activities 
involving endangered and threatened wildlife species under certain 
circumstances. Regulations governing permits for endangered species are 
codified at 50 CFR 17.22. With regard to endangered wildlife, a permit 
may be issued for the following purposes: For scientific purposes, to 
enhance the propagation or survival of the species, and for incidental 
take in connection with otherwise lawful activities. For threatened 
species, a permit may be issued for the same activities, as well as 
zoological exhibition, education, and special purposes consistent with 
the ESA.

National Environmental Policy Act (NEPA)

    We have determined that environmental assessments and environmental 
impact statements, as defined under the authority of the National 
Environmental Policy Act of 1969 (42 U.S.C. 4321 et seq.), need not be 
prepared in connection with regulations adopted under section 4(a) of 
the ESA. We published a notice outlining our reasons for this 
determination in the Federal Register on October 25, 1983 (48 FR 
49244).

References Cited

    A complete list of all references cited in this proposed rule is 
available on the Internet at http://www.regulations.gov or upon request 
from the Branch of Foreign Species, Endangered Species Program, U.S. 
Fish and Wildlife Service (see FOR FURTHER INFORMATION CONTACT.)

Authors

    The primary authors of this final rule are Amy Brisendine and 
Natchanon Ketram, Branch of Foreign Species, Endangered Species 
Program, U.S. Fish and Wildlife Service.

List of Subjects in 50 CFR Part 17

    Endangered and threatened species, Exports, Imports, Reporting and 
recordkeeping requirements, Transportation.

Regulation Promulgation

    Accordingly, we amend part 17, subchapter B of chapter I, title 50 
of the Code of Federal Regulations, as set forth below:

PART 17--[AMENDED]

0
1. The authority citation for part 17 continues to read as follows:

    Authority:  16 U.S.C. 1361-1407; 1531-1544; 4201-4245; unless 
otherwise noted.


0
2. Amend Sec.  17.11(h) by adding entries for ``Macaw, great green'' 
and ``Macaw, military'' in alphabetical order under BIRDS to the List 
of Endangered and Threatened Wildlife to read as follows:


Sec.  17.11  Endangered and threatened wildlife.

* * * * *
    (h) * * *

 
--------------------------------------------------------------------------------------------------------------------------------------------------------
                   Species                                       Vertebrate  population
----------------------------------------------  Historic range    where  endangered or        Status       When  listed      Critical     Special  rules
         Common name          Scientific name                          threatened                                             habitat
--------------------------------------------------------------------------------------------------------------------------------------------------------
 
                                                                      * * * * * * *
 
            Birds
 
 
                                                                      * * * * * * *
Macaw, great green..........  Ara ambiguus     Costa Rica,      Entire                                 E             797              NA              NA
                                                Honduras,
                                                Nicaragua, and
                                                Panama.
 
                                                                      * * * * * * *
Macaw, military.............  Ara militaris    Argentina,       Entire                                 E             797              NA              NA
                                                Bolivia,
                                                Colombia,
                                                Ecuador,
                                                Mexico, Peru,
                                                Venezuela.
 
                                                                      * * * * * * *
--------------------------------------------------------------------------------------------------------------------------------------------------------

* * * * *

    Dated: September 17, 2015.
Stephen Guertin,
Director, U.S. Fish and Wildlife Service.
[FR Doc. 2015-24820 Filed 10-1-15; 8:45 am]
 BILLING CODE 4310-55-P