[From the U.S. Government Printing Office, www.gpo.gov]
TECHNICAL REPORT
A SURVEY OF THE
DOG RIVER WATERSHED
Second Year's Findings



A Review of Ongoing Development in the Basin
and an Assessment of the Effects
of Urban Non-Point Sources on
the Aquatic Resources of the Basin





COASTAL PROGRAM
November 1995



ALABAMA DEPARTMENT OF ENVIRONMENTAL MANAGEMENT
1751 CONG. W. L. DICKINSON DRIVE ï¿½ MONTGOMERY, AL 36130

US Department of Commerce
NOAA Coastal Services Center Library
2234 South Hobson Avenue
Charleston, SC 29405-2413

A SURVEY OF THE
DOG RIVER WATERSHED
Second Year's Findings


A REVIEW OF ONGOING DEVELOPMENT
IN THE WATERSHED
AND AN ASSESSMENT OF THE EFFECTS
OF URBAN NON-POINT SOURCES ON
THE AQUATIC RESOURCES OF THE BASIN




COASTAL PROGRAM
ALABAMA DEPARTMENT OF ENVIRONMENTAL MANAGEMENT
November 1995
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Planning And Ecnomaic
reVQi0pmnit OMlion
This report was funded in part by the Alabama
Department of Economic and Community Affairs,
Office of the Governor, State of Alabama,
and in part by a grant from the Office of Ocean and Coastal
Research Management, National Atmospheric and Oceanic
Administration, United States Department of Commerce.
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DISCLAIMER

The mention of trade names or brand names in this document is for illustrative
purposes only and does not constitute an endorsement by the Alabama Department of
Environmental Management, the Alabama Department of Economic and Community
Affairs or the National Oceanic and Atmospheric Administration.

TABLE OF CONTENTS
List of Tables and Figures	11
Executive Summary	I
Introduction and Overview1
Ongoing Development and Impacts to the Watershed	3
Land Clearing, Stream Siltation and Water Clarity	6
Impervious Cover, Increased Runoff and Streamflow	10
Municipal Infrastructure and Water Quality          I11
Sediment Chemistry	12
Materias and Methods	13
Results and Di-scussion	16
Benthic Biology	25
Introduction	25
Objective	25
Materials and Methods	26
Results and Discussion	28
Review and Conclusions	38
Bibliography	40
I

LIST OF TABLES AND FIGURES
TABLES
Table 1: Site Locations for Sediment Cores and
Benthic Macroinvertebrate Samples
Table 2: Metals Data for Dog River Watershed Sediments
Table 3: Summary Statistics for Benthic Macroinvertebrate
Communities
Table 4: List of Benthic Macroinvertebrate Species Collected
from the Dog River Watershed
Tables 5a-5f: Site Lists of Benthic Macroinvertebrates Collected
Table 5a: Rabbit Creek Station
Table 5b: Halls Mill Creek Station
Table 5c: Dog River Station DR- 1
Table 5d: Moore Creek Station
Table 5e: Dog River Station DR-2
Table 5f: Dog River Station DR-3

FIGURES
Figure 1: Coastal Alabama Showing the Dog River Watershed
Figure 2: The Study Area Showing Major Roads and Streams
Figure 3: The Study Area Showing City Streets, County Roads
and Secondary Roads '
Figure 4: Locations of Sites Sampled for Sediments
and Benthic Infauna
Figures 5a-5h: Sediment Metal Plots for the Dog River Watershed
Figure 5a Arsenic
Figure 5b: Barium
Figure 5c: Cadmium
Figure 5d: Chromium
Figure 5e: Copper
Figure 5f: Lead
Figure 5g: Nickel
Figure 5h: Zinc
Figures 6a-6h: Benthic Invertebrate Community Statistics
Figure 6a: Infaunal Abundances
Figure 6b: Number of Benthic Taxa
Figure 6c: Shannon Community Diversity
14
17


28


33
35-37
35
35
36
36
37
37


2
5

6


15
21-24
21
21
22
22
23
23
24
24
29-30
29
30
30
II

Executive Summmary
The Dog River Watershed, a basin located in an area with extensive commercial
and residential development, was surveyed for an evaluation of the stresses of urban
growth on the streams of the basin. Active construction sites were found to have a
significant impact on water clarity and streambed siltation. Lack of effective erosion
control at project sites was the single most responsible contributor to the degradation
of stream habitat. Erosion and siltation furthermore appear to pose a potential threat
to waterfront property and wetlands. Existing development and historical land-use
practices also have left their mark on the aquatic fauna and stream bottom habitats of
the basin. Analysis of sediment cores from streanis of the watershed indicated a
conspicuous enrichment of lead, zinc and other metals characteristic of urban runoff.
Examination of the benthic infauna revealed low overall abundances, depressed
community diversity and dommnance by pollution tolerant species at some stations.
Conditions considered by many biologists as emblematic of aquatic habitats affected
by streambed siltation, organic enrichment and other aspects of urban runoff.
III

Introduction and Overview
The Dog River Watershed (Figure 1) has been studied since 1993 by the
Alabama Department of Environmental Management's Coastal Program. The project
was designed to assess the effects of land-use practices and developiment on the
aquatic resources of the watershed. This was accomnplished through determining the
physical characteristics of the watershed (i.e., topography, soil types, etc.), reviewing
past and present land-use practices, inspecting active construction sites, monitoring
the effects of non-point sources on the basin's water and sediment quality, surveying
the wetlands flora and examining the benthic infaLunal community of the watershed.
In the first report, entitled A Survey of the Dog River Watershed - An Overview of
Land-Use Practices and the Affects of Development on the Natural Resources of the Basin
and published in May, 1994, the historical development and recent land-use practices
of the Dog River Watershed (DRW) were reviewed and the impacts of such activities on
the aquatic habitats and water quality of the basin were examined. The findings of the
first report revealed that streambed siltation and impairment of water clarity (turbidity)
from non-point sources in the watershed pose the most significant threat to aquatic
life and water quality. Erosion and storm runoff from construction sites are the
primary contributors to the saltation and turbidity problem. Secondary impacts
include degradation of aesthetics due to trash and litter in the water, elevated nutrient
concentrations in storm water runoff, loss of natural shoreline habitat due to bulkhead
and fil developments and impairment of recreational uses of surface waters due to
bacterial (fecal coliform) contamination.
In this second report, ongoing development and construction within the basin
are more closely examined. The potential of these activities for promoting additional
losses of stream habitats and contributing to water quality degradation effects are
taken into account. Also discussed in this report are the results of a survey of the
benthic inifaunal communities and sedimnent chemistry of streams in the watershed.
I

Figure 1
Coastal Alabama showing the Dog River Watershed











2

Ongoing Development and Impacts to the Watershed
Land Clearing. Stream Siltation and Water Claritv

The focus of the second year of the study was directed at the areas of the
watershed experiencing the most active growth and development. The western and
southern portions of the watershed continue to experience extensive real estate
development in the form of light industrial parks, office buildings, retail businesses
(shopping centers) and residential subdivisions.
As is typical with these activities, significant acreage is cleared during site
preparation including the removal of all undergrowth and ground cover along stream
banks. Uncontrolled, such practices subject large areas of cleared land to erosional
processes. Erosion is a pervasive problem in actively developing areas of the DRW due
to the erodible sandy-loam type soils, rolling topography and the intense rainstorms
common to Mobile County. The result has been, and continues to be, that soil laden
runoff from construction projects drains to nearby streams. Soil losses of 42 lbs/acre
from a single storm-event have been measured at residential developments in Mobile
County (South Alabama Regional Planning Commission, 1989). Annual loss rates of
soil from construction sites may be as high as 50 tons per acre (US Fish and Wildlife
Service, 1990).
During the watershed survey, all known construction projects of an area
greater than five acres in the DRW were inspected by ADEM personnel. Construction
sites of such size are now regulated under the NPDES General Permit Program which
requires these activities to utilize various industry standard methods of erosion
control, soil stabilization and detention of stormwater runoff. Methods proven effective
in the control of runoff from cleared areas include sodding, seeding and mulching,
applying soil binders or 'tackifiers", silt fences and maintaining uncleared vegetated
boundaries or greenbelts. The term Best Management Practices (BMP) has been
applied to the devices and techniques employed for the control of erosion and runoff
from construction sites and developed property.
Many of the sites inspected were found to have inadequate measures for
control of erosional runoff and stream siltation. A common problem at sites where the
contractor had attempted some means of BMP was improper installation of silt fences
and hay bales. Silt fences often were set in place without burying the bottom edge flap
allowing storm water to run underneath the silt fence. In more than one case, wash-
outs formed under silt fences leaving the bottom of the fence suspended above the
3

ground. Contractors also were somewhat negligent seeding, mulching and sodding the
bare ground after clearing and grading operations. In a few cases the contractor
properly installed these devices and initiated BMPs at the beginning of a project but
failed to maintain such practices as the job progressed. In general the problem was
that little if any detention of stormwater runoff nor effective stabilization of cleared
ground was observed at construction sites.
Halls Mill Creek (Figure 2) appears to be the recipient of the majority of the
sediment burden currently discharged to the DRW. Surveys of the Halls Mill Creek
sub-basin show that siltation has significantly affected Halls Mill Creek for over half its
length, from below the 1- 10 bridge to its uppermost reaches near the western
boundary of the city limits. The numerous recently completed and ongoing
construction projects in the Halls Mill Creek sub-basin have released a considerable
quantity of soil to the system.
Currently, the most active development within the watershed is occurring near
Milkhouse Creek and Second Creek, the main tributaries to Halls Mill Creek (Figure
2). These streams receive drainage from the land along Mobile County Road 31
(Schillinger Rd.) and Co. Rd. 37 (Cody Rd.), see Figure 3. A sizable amount of these
projects involve clearing, grading and excavating along stream courses. At the time of
the survey there were nine subdivisions undergoing development, ongoing road
improvements including a new bridge across Milkhouse Creek and construction of an
office complex. Inspections of construction sites by ADEM staff revealed that most of
these projects were started without any attempts of controlling erosion. The few
contractors initiating BMP measures at the beginning of a job neglected to maintain
these devices and failed to expand coverage of stormwater control to keep up with the
growth of the project. The result being a lack of control of erosion and runoff after just
a few days of installation.
4

Figure 2
Dog River Watershed
Major Streams and Highways are Shown










5

Figure 3
Dog River Watershed
City Streets, County & Secondary Roads









6

Other problems related to construction activities arise from connecting
subdivision utilities to public systems. At somne of the proect sites, fil roads were
construicted and pipeline trenches excavated across stream courses and associated
wetlands for access to municipal sanitary mains. During the course of sewer tie-in
operations contractors paid little attention to controlling erosion from the project site.
It was observed that considerable amounts of road fll and trench spoil have been
washed by rain to creeks and wetlands.
These projects also have the potential for short term but significant discharges
of untreated sanitary sewage. During tie-in operations it often is necessary to divert
flow of the sewer main around the site. This usually is accomplished by means of a
bypass line for routing sewage from "upstream" of the tie-in to a point in the main
'downstream" of the site. At some project sites leaks and overflows from bypass lines
were observed to discharge sewage to area streams causing noticeable degradations in
water quality. On other occasions, careless actions by contractors resulted in
disconnected and/or broken sanitary lines. Activities such as these are potential
explanations for some of the high fecal coliform numbers obtained during the first year
of the survey. Additional discussion of the problem of sanitary wastes in the streams
of the watershed will be found later in this report.
Other streams in the DRW also receive a considerable amount of urban runoff
and sedimentation. Moore Creek is dredged by the City of Mobile because of sediment
accumulations restricting the capacity of the creek. If not removed, the sand bars and
silt deposits have the potential for impeding drainage of storm runoff from the
surrounding area.
The neighborhoods in the Moore Creek sub-basin are older than those along
Milkhouse and Second Creeks; consequently there is less ongoing construction
because of the more developed nature of the locale. However, the high density
housing, asphalt parlcing lots and paved roads typifying the development in the Moore
Creek area are known to contribute significant sediment loads to streams via
increased runoff from storms. The conversion of natural surface drainage (i.e., sheet
flow) to storm drains, culverts and drainage canals (i.e., channelized flow) disrupts
existing stable drainage courses and accellerates erosion through scour (Alabama
Department of Environmental Management 1989; South Alabama Regional Planning
Commission, 1989 and US Fish and Wildlife Service, 1990). This problem is typical of
urban areas and demonstrates the need for control of stormwater runoff from
developed areas and not just construction sites.
7

Although Eslava Creek has been "urbaniized~ longer than other streamns of the
DRW it was less affected by turbidity and siltation compared to the rest of the streams
in the watershed. However, ongoing and planned development between Mobile County
Roads 56 (Airport Boulevard) and 70 (Old Shell Road) in the vicinity of 1-65 pose a
potential for such problems. Proper installation and maintenance of erosion and
runoff control BMPs will help avoid additional degradation to a stream which has long
been affected by development and urban runoff.
Trash and litter continue to be the number one pollution problem in Eslava
Creek, Bolton Branch and the uppermost segments of the Dog River. Considerable
quantities of plastic wrapping, plastic bottles, styrofoam cups and assorted paper
items appear in these streams following a rain storm. Most of this material comes from
parldng lots and curb gutters along upper Eslava Creek and is transported to the creek
by storm runoff through drains and culverts.
During the first year of the survey of the DRW the Rabbit Creek/ Rattlesnake
Bayou system was found to be the least developed sub-basin in the watershed. Not
surprisingly, it also has experienced the least amount of aquatic habitat and water
quality degradation of the major tributaries to the Dog River. Historicaly the
development in the Rabbit Creek/ Rattlesnake Bayou watershed has been low to
mnoderate density residential with a few light industrial-commercial facilities.
More recently there has been a surge of commercial development in the area as
construction has begun on several new warehouses along U.S. Hwy 90 and a light
industrial park between Mobile County Road 26 (Hamilton Blvd.) and Rangeline Road
has opened. Initial inspection of these sites revealed that the BMP employed by the
contractors were inadequate and provided little or no colAtrol of erosion and soil loss
from the project site to local waters. Follow-up inspections have indicated that
somewhat more effective measures have been taken by the contractors to control
siltation from cleared areas.
If development in the Rabbit Creek/ Rattlesnake Bayou watershed continues its
recent rate of progress and if BMPs are not more scrupulously followed then it is
inevitable that losses of wetlands, aquatic grassbeds and benthic habitats, similar to
those losses observed in the Halls Mill Creek system, will occur.
The damage caused by erosion and siltation affects both wildlife and humans.
The deposition of sand and silt smothers submersed vegetation, gravel riffles and other
productive stream-bottom habitats. Even those bottom dwelling (benthic) species
capable of inhabiting severely stressed environments are prevented from colonizing
stream bottoms subjected to heavy siltation. The inability of 'base of the food chain
8

species for establishing a population coupled with the destruction of important habitat
such as grassbeds eventually leads to a loss of the larger recreationally and
commercially important species. This will be further discussed in the section on
benthic biology later in this report.
The ever increasing volumes of sediment in streams receiving such runoff also
raise the elevation of the stream bed thereby decreasing the capacity of the original
channel. This process effectively raises the elevation of the water surface under all
flow regimes and particularly so during high flows following storm events. This
condition has the ability to increase the frequency and severity of flash floods and
impair navigation along affected stream courses. If allowed to continue, siltation might
raise the water level of creeks during storms thereby increasing the potential for
inundating roads, bridges and private property. Sedimaent laden waters overbanking a
stream also lay down sand and silt on the flooded land as the waters recede. The
processes of erosion and siltation observed in streams of the DRW have the ability to
constitute threats to property above and beyond the damage done to stream
aesthetics.
The erosional processes at construction sites also has an affect on water clarity.
Marked turbidity increases in the streams drainfing active developments are apparent
of the DRW following significant rainfall (>0.25"); this is especially the case in the
Hall's Mill Creek sub-basin and its tributaries Milkhouse Creek, Second Creek and
Spring Creek. Monitoring of construction sites and receiving streams in the DRW by
ADEM personnel has shown that turbidity increases of maore than 2000 NTUs may
occur in streams affected by uncontrolled runoff from land clearing activties
(Milkhouse Creek and Second Creek).-
Extremely tuirbid waters not only are an impediment to photosynthesis by
subinersed vegetation and phytoplankton but also are aesthetically unappealing. The
persistence of streara turbidity due to clay fines suspended in the water may be
evident miles from the construction activities causing the problem. High altitude
photographs of the watershed indicate a turbidity plume extending from Halls Mill
Creek into Dog River and down river to Mobile Bay. Following heavy rainfall in the
watershed the turbidity in Halls Mill Creek is sufficient to produce a visible plume in
the Dog River below their confluence, over 5 miles from the developmnents in western
Mobile.
9

Imuervious Cover. Increased Runoff and Streamflow
The increasing amnount of impervious cover created by development reinforces
the need to control siltation and avoid further restricting the drainage in the
watershed. Much of the developed property in the DRW, especially the Halls Mill
Creek sub-basin, includes sizable areas of parking lots, streets, sidewalks, rooftops
and other impervious cover. In some cases property development includes substantial
alteration of the natural drainage and consolidation of several smaller drainage
courses and sheet flow into a single larger course. The storm water runoff from some
of the commercial areas and residential neighborhoods is remarkable during heavy
rains. This runoff was observed to substantially increase the rate of flow in the
tributaries of the DRW compared to base flow conditions.
It is well documented in studies of urban runoff and stream hydrology that the
impervious cover created by development can result in severe increases in stream flow
during storms relative to base flow conditions (Alabama Department of Environmental
Management, 1989; South Alabama Regional Planning Commission, 1989 and US Fish
and Wildlife Service, 1990). Information searches conducted for the study yielded no
historical records of flows in the DRW and this study did not quantify flows in the
surveyed streams. Interviews with long-term residents living along Halls Mill Creek
have indicated that the level of the creek in recent years has risen to higher levels
during rainstorms than in the past.
Increased variability between a stream's base flow condition and its high flow
level due to storm runoff presents an intrinsic probletm with stream bank erosion. The
sudden increases in flow combined with a rapidly fluctuating water level act to
undercut stream banks and erode bank-side vegetation (Alabama Department of
Environmental Management, 1989 and South Alabama Regional Planning
Commission, !989). Although such processes occur naturally, the acute increases in
stream-flow resulting from urban stormwater runoff accelerate the rate of streambank
erosion.
This represents a threat to property owners from the erosional loss of shoreline
and a danger to aquatic life from scouring and "blow-out" during storm events.
Increased channelization of storm runoff and increased runoff from greater areas of
impervious cover also act to uncover and wash out buried utilities (see discussion of
municipal infrastructure beloxv) and undermine supports for bridges.
10

Municirual Infrastructure and Water Ouahitv
The first year's study of the DRW disclosed a problem with enteric bacteria in
streams of the basin. On several occasions the colony counts of fecal coliform samples
were above the single sample maNimum for a stream's use-classification. Studies of
urban non-point sources have found thaLt in some instances high counts of fecal
cohiforms are attributable to domest-ic amimals. These bacterial problems frequently
manifest themselves following heavy rains and the numbers diminish after stormf lows
subside. High fecal coliform readings persistent ove-r days or weeks are. more
indicative of contamination from lealks in sanitary sewers, sewer back-ups and
overflows due to sediment and trash in sewer lines, sanitary connections to storm
sewers and failing septic tanks.
The persistence of high fecal coliform readings observed at some of the
monitoring statilons during the first year indicated that some of the bacterial problems
might be ascribed to humans more than to animals. This was the case in particular
with Moore Creek and Halls Mill Creek.
As mentioned earlier in the report, connecting subdivisions to the municipal
sanitary system has the potential for making significant short-term contributions to
the pollution of a stream. Inspections of construction sites revealed that this process
is often repeated around the watershed. Loose fitting couplings and leaks in flexible
pipe utilized for the bypass were the usual cause for the discharge of sanitary waste
during tie-in operations.
Investigation of citizens' complaints relative to sewage odors in the Cottage Hill
area led ADEM and the Mobile Area Water and Sewer System (MAWSS) to the
discovery of broken sanitary sewer lines along Milkhouse Creek and across Moore
Creek near Mobile Counly Road 28 (Halls Mill Road). Undermining of the sewer pipe
by storm runoff leaving several sections of the pipe unsupported was the cause of the
line breaks. The duration these leaks existed is uncertain; however, once they were
discovered, repairs were made to the damaged components and the sewer lines were
returned to service.
This illustrates another complication of urban development and the large areas
of impervious cover it creates. Collecting storm runoff in draiuage systems and routing
it to streams creates the potential for damaging utilities and infrastructure through
excessive hydraulic force, erosioln and undermining action.
Aging of the sanitary sewer system also has contributed to the impairment of
water quality in the watershed. Lift stations on Second Creek and Halls Mill Creek are
11

known to have discharged to their respective streams due to leaks, overflows and
pump failures. Repairs on these facilities are near completion and should result in
improvement of these streams, particularly with respect to enteric bacteria,
A comprehensive survey of the municipal sanitary system by the MAWSS is
ongoing. The survey is to more accurately determine the routes of sewer lines, locate
leaks, overflows and find interconnections between the storm and sanitary systems.
Problems facing the MAWSS are sewer lines dating to near the turn of the century in
older neighborhoods, incomplete and missing plans for some portions of the system,
improper installation of sanitary lines by contractors in subdivisions and sanitary
connections made to storm sewers.

Sediment Chemistry

Examination of sediments can offer insight into past conditions as well as
indicating the present 'pollution climate" because sediments represent a temporally
integrated record of chemical conditions in a watershed. Many contaminants entering
a watershed become sequestered in the sediments. This particularly is the case with
estuarine watersheds as salt water promotes adsorption and precipitation of materials
dissolved in the fresh water entering the system.
The objective of the sediment sampling program was to determine the
concentrations of metals and the presence of excessive metal enrichment. These
results were compared to a survey of natural estuarine sediments in the Alabama
coastal zone which established the existence of statistically significant relationships
between aluminum and eight trace metals: arsenic, barium, cadmium, chromium,
copper, lead, nickel and zinc (Alabama Department of Environmental Management,
1991). These relationships may be utilized to identify unnatural concentrations of
metals in estuarine sediments (Schropp and Windom, 1988 and ADEM, 1991).
This method of interpretation is based on the naturally occurring relationships
between aluninum and other metallic elements. The basis for this method is that
aluminum occurs naturally in all estuarine sediments and the concentrations of other
metals tend to vary with the concentration of aluminuim. These naturally occurring
proportions of metals relative to aluminum have been reported by several
investigators, Turekian and Wedepohl (1961), Taylor (1964), Duce et al (1976) and
Schropp and Windom (1988) to be fairly constant. These relationships allow for the
use of aluminum as a reference element or "normalizing factor" for identification of
sediments enriched by anthropogenic activities. This concept has been used to
12

examine metal pollution in the Savannah River estuary (Goldberg, 1979), lead
pollution in the Mississippi River (Trefey et al., 1985) and metal pollution in Florida
estuaries (Schropp and Windom, 1988). Additional detail regarding this technique
may be found in Schropp and Windom (1988) and ADEM (1991 and 1992).

Materials and Methods

On September 30, 1994 sediment samples were collected from seven stations
in the DRW. Sediments were collected from seven sites in the watershed, three
locations on Dog River and one each on Moore Creek, Robinson Bayou, Halls Mill
Creek and Rabbit Creek (Figure 4 and Table 1). Stations were selected to be
representative of overall stream conditions and not localized or isolated problems such
as boat slips, dredged channels and storm drains. Station depth was between 1.5 and
2.5 meters at each site except Robinson Bayou which was only 0.75 meter deep.
Sediment cores were retrieved with a K-B type core sampler (Wildlife Supply
Co., cat. no. 2402-A12) equipped with a cellulose-acetate-butyrate liner tube.
Sediment for metal analyses was taken from the upper five centimeters (2 inches) of
each core, placed in an acid-washed glass jar and capped with a Teflon lined lid.
Samples were collected in triplicate, two samples for immediate processing and the
third sample for 'archiving" in a freezer for future analyses in case of widely varying
results between the first two.
13

TABLE I
SITE LOCATIONS FOR SEDIMENT CORES
AND BENTHIC MACROINVERTEBRATE SAMPLING

STATION DESIGNATION                  LOCATION
DR-1                 DOG RIVER, I/ 2 MILE DOWNSTREAM OF
THE CONFLUENCE WITH HALLS MILL
CREEK AND APPROX. 1/4 STREAM
WIDTH OUT FROM THE EAST (LEFT)
RIVER BANK.
DR-2                 DOG RIVER, I MILE UPSTREAM OF THE
CONFLUENCE WITH ROBINSON BAYOU
AND APPROX. 1/4 STREAM WIDTH OUT
FROM THE WEST (RIGHT) RIVER BANK.
DR-3                 DOG RIVER, 1/4 MILE DOWNSTREAM OF
1-10 BRIDGE CROSSING AND APPROX.
1/4 STREAM WIDTH OUT FROM THE
EAST (LEFT) RIVER BANK.
RB                   ROBINVSON BAYOU, 1/4 MILE UPSTREAM
OF THE MOUTH OF THE BAYOU AND AT
MID-STREAM.
Mc                   MOORE CREEK, 1/2 MILE UPSTREAM OF
THE MOUTH OF THE CREEK AND
APPROX. I/ 4 OF THE STREAM WIDTH
OUT FROM THE WEST (RIGHT) CREEK
BANK.
HMC                  HALLS AILL CREEK, I MILE UPSTREAM
OF THE MOUTH OF THE CREEK AND
APPROX. 1/4 OF THE STREAM WIDTH
OUT FROM THE SOUTH (RIGHT) CREEK
BANK.

RC                   RABBIT CREEK, 2 MILES UPSTREAM OF
THE MOUTH OF THE CREEK AND APPROX.
1/4 OF THE STREAM WIDTH OUT FROM
THE NORTH (LEFT) CREEK BANK.
14

Figure 4
Locations of sites sampled for sediments
and benthic infauna.









15

Sample analyses began with oven-drying of sediments at 60 degrees Celsius.
Weighed portions (250 mg) of each sample were placed in Teflon bombs and subjected
to a total digestion process in a solution of nitric acid, hydrofluoric acid and perchloric
acid at 120 degrees Celsius. Analyses were performed with a Perkin-Elmer 3030-B
atomic absorption spectrophotometer (AA) equipped with a flame furnace for Al, Fe and
Zn and a graphite furnace for As, Ba, Cd, Cr, Cu, Pb, Ni and Sn. A Leeman Labs Model
PS-200 automated mercury analyzer was utilized for Hg analyses.
The mean values of the analyses of replicate samples were utilized as data for
statistical comparisons. Statistical procedures employed in this study are detailed in
Sokal and Rohlf (1969) and Filliben (1975).


Results

Results of sediment metal analyses are listed in Table 2 The concentrations of
eight trace metals were compared to the concentration of aluminum as described in
Schropp and Windom (1988) and ADEM (1991) for determining whether sediments of
the watershed were enriched with trace metals. Graphical plots of these relationships
are illustrated in Figures 5a-h. Superimposed on the data plots are regression lines
and 95% confidence bands for each metal/aluminum relationship as would be
expected to occur in uncontaminated sediments. The basis for determining these
relationships are described by Schropp and Windom (1988) and ADEM (1990).
16

TABLE 2





STATIN Al As Ba Cd Cr Cu Fe Hg Mn Ni Pb Sn Zn
DR- 1     43,450 8.0   224 0.37 29 2 1 29,350 0.18   282 8.8 34 2.3 115
DR-2 55,750 9.1 254    1.47   37 43 34,800 0.40 276	20.5 142 5.2 336
DR-3 10,950   1.5 124 0.59 13 13 6,150 0.11    73	5.0	5 1 2.2 94
HMC       63,150 9.0	199 0.40 3 1 28 37,200   0.25 117 13.0	46 3.0 138
Mc 16,900	2.6	80   0.36	15 I11   9,850 0.07	7 1	5.0 38 1.7	88
RB 52,200	9.1 220 1.12	32	58 31,050 0.32	260	20.5 114	3.6	326
RC 45,050 10.6 137   0.51	27	20 36,150 0.28	413	8.0	4 1	2.5 117
AVG	41,064 7.1 177 0.69 26	28	26,364 0.23	213	11.5	66	2.9 173
MAX	63,150 10.6 254 1.47	37	58	37,200 0.40	413	20.5 142 5.2	336
N41N 10,950    1.5          $0  0.36	1 3	1 1	6,'150   0.07	7 1	5.0   34 1.7	88

ANl values are exDressed as malka drv wt.
ANl values are the avemase of dunficaie samvles
There is no accompanying plot for the mercury data The findings of previous
sediment studies by Schropp and Windom (1988) and the Department (ADEM, 1991)
have shown that a relationship between mercury concentration and aluminum
apparently does not exist. This is a consequence of the scarcity of naturally occurring
mercury in the Mobile Bay drainage basin (Isphording, personal communication) and
the fact that natural mercury concentrations are often near the limit of analytical
detection where accuracy and precision are reduced.
Aluminum concentrations in sediments of the watershed ranged from 10,950 to
63,150 parts per million (PPM) measured as milligrams per kilogram (mg/kg) of dry
sediment. Sediments from Moore Creek and upper Dog River contained the lowest
aluminum concentrations reflecting the coarser nature of these sediments. The finer-
grained sandy-silts and clays of Robinson Bayou, Halls Mill Creek and the lower half of
the Dog River contained higher concentrations of aluminum.
Concentrations of arsenic, barium, chromium and nickel at all stations fell
within or below expected natural ranges, based on the metal to aluminum
relationships. The sediments of Robinson Bayou and the upper half of the Dog River
contained cadmium in amounts above the range to be expected in natural sediments.
Sediment from all sites sampled in the watershed were found to have concentrations of
17

copper, lead and zinc that are higher than expected for natural sediments in coastal
Alabama.
Cadmium is a trace metal utilized in a variety of products, plastics, ceramics,
paints, pesticides and storage batteries to name a few. It also may be present in
phosphate rock used for fertilizers and is a product of the comabustion of fossi fuels
(Canadian Council of Resource and Environment Ministers-CCREM, 1987). The major
contributors of cadmium to urban watersheds are combustion contaminants in storm
runoff from streets and parking lots, and runoff of fertilizer and pesticides from
landscaped property (US Environmental Protection Agency, 199 1; US Fish and Wildlife
Service, 199 1; Florida Department of Environmental Protection, 1993 and Baudau and
Muntau, 1990).
Researchers in the field of sediment chemistry and toxicity have established
that a concentration of 5 ppm (mg/kg) cadmium is potentially unfavorable for aquatic
life and that adverse effects to aquatic life are likely to occur above 9 ppm (mg/kg)
cadmium (Long and Morgan 1990). Referenced to these findings, the cadmium
enrichment detected in the DRW, although conspicuous, is well below levels of
concern.
Copper is widely used in wood preservatives, pesticides, soil fungicides,
algaecides for controlling slime in cooling systems and anti-foulant surface coaangs for
boat hulls and submersed structures. Runoff containing fungicides and pesticides,
and 'leaching out" of wood preservatives and marine antifoulants from treated
materials are the primary means by which copper enters urban watersheds (CCREM,
1987; Shutes et al., 1993; US Environmental Protection Agency, 199 1; US Fish and
Wildlife Service, 199 1; Florida Departmnent of Environmental Protection, 1993 and
Baudau and Muntau, 1990).
The highest concentration of copper found in the watershed was 58 ppm
(mg/kg). The recommended concentration of copper for which no adverse biological
effects should be observed is 70 ppm (mg/kg) (Long and Morgan 1990). A
concentration of 390 ppm (mg/kg) copper in sediments has been established as a level
at which adverse biological effects are likely to occur (ibico. Hence the copper in
sediments of the DRW, although present in elevated amounts, is not considered "toxic"
to aquatic life.
Lead is commonly a constituent of paints, dyes, plastics and solder. The single
largest use of lead in the US is in lead-acid storage batteries. Prior to the trend
towards unleaded gasoline over the past two decades the use of tetraethyl lead in
motor fuel accounted for the single largest source of lead to the environment (Baudau
is

and Muntau, 1990; CCREM 1987). Most of the lead in our waterways is the result of
exhaust deposits washed from urban areas by stormwater runoff (Baudau and
Muntau, 1990; CCREM 1987; Shutes et al., 1993; US Environmental Protection
Agency, 1991; US Fish and Wildlife Service, 1991; VanHassel et al.,1980). The
'phasing oute of lead in gasoline is gradually removing this source from further
polluting waterways as well as the atmosphere. The use of lead as a pigment in paints
and other surface coatings will continue to leach lead to aquatic environments (US
Environmental Protection Agency, 1991; Baudau and Muntau, 1990).
Research has tentatively established a concentration of 35 ppm of lead in
sediment as a level below which no adverse effects to aquatic life are likely to occur.
Lead concentrations exceeding 110 ppm in sediments has been found to be potentially
harmful to amphipods (Becker et al., 1990 and Long and Morgan, 1990) brown shrimp
(Vittor and Assoc., 1988), bivalves and numerous other species of aquatic animals
(Chapman et al., 1987 and Long and Morgan, 1990). All but one of the sites sampled
in the DRW were above the lower threshold and two of these (RB and DR-2) exceeded
the upper threshold with values of 114 ppm and 142 ppm respectively.
Zinc is an important constituent of anti-corrosive coatings for iron and steel
products. Applications include marine paints, metal roofing and steel girder
structures. Zinc is widely utilized as a biocide and anti-corrosion additive in
commercial cooling systems and boilers. As was the case with copper and lead,
stormwater runoff from urban areas with a high usage of these materials is the
primary path by which zinc enters aquatic environments (Shutes et al., 1993; US
Environmental Protection Agency, 1991; US Fish and Wildlife Service, 1991;
VanHassel et al., 1980).
Long and Morgan (1990) have established a recommended lower threshold for
zinc in sediments of 120 ppm and an upper threshold, above which adverse effects are
likely, of 270 ppm. Two of the sites sampled (DR-2 and RB) exceeded the upper
threshold with values of 336 ppm and 326 ppm respectively. Chapman et al. (1991
and 1987), McLeay et al. (1991), Shutes et al. (1993) and other researchers have
demonstrated that zinc concentrations such as these are potentially harmful to
crustaceans (amphipods and grass shrimp) and mollusks.
The affects of urban development and non-point sources are evident from the
results of the sediment survey. Conditions such as those observed in the DRW are
representative of other coastal watersheds with a high degree of urbanization (Long
and Morgan 1990; Delfino et al. 1991; US Environmental Protection Agency 1991; US
Fish and Wildlife Service 1991; Florida Department of Environmental Protection 1993).
19

Considering the lack of heavy industrial facilities in the DRW and the high
degree of urban development with large areas of impervious cover, landscaped
property maintained with intensive use of chemicals, high density of motor vehicular
traffic and power boating activity, it appears that the sediment contamination observed
in the watershed is largely attributable to storm water runoff flushing contaminants to
streams of the basin. These contaminants are derived from exhaust soot and residue
from paved surfaces, fungicides, insecticides and other biocidal preparations,
fertilizers and wood preservatives. Lesser but still significant inputs of metallic
contaminants are ascribable to wood preservatives leaching from piling and bulkheads
and the anti fouling/anti corrosive components of marine paints (Shutes et al. 1993;
US Environmental Protection Agency 1991; Delftno et al. 1991; Baudau and Muntau
1990; National Oceanic and Atmospheric Administration 1989; National Research
Council 1990; Windom et al. 1989; VanHassel et al., 1980).
Due to the expected development in the basin these conditions are likely to
persist and possibly could become more outstanding in the future.
20

Figure 5a Arsenic
IALUMINUM/BARIUM I
1000 --

Y = 0.00407X + 4.259269

750 --




0)
E
 500--





DR-1     ~ - BR'~'J'     _







0            20,000          40,000          60,000          80,000         100,000
Aluminum (mg/kg)



Figure 5b Barium


Sediment Metals Plots for the Dog River Watershed
21

ALUMINUM/ICADM IUM




Y =0.0000068X - 0.652876




E                                       * ~~~~~~~~~~~~DR-2





-1o.0-






0             20,000           40,000           60,000           80,000           100,000
Aluminum (mglkg)
Figure 5c Cadmium
IALUMINUM/CHROMIUM




125--


100-


75.

00

DR-2







0              20,000             40,000            60,000             80,000             100,000
Aluminum (mgtkg)
Figure 5d Chromium

Sediment Metals Plots for the Dog River Watershed
22

ALUMINUM/COPPER

75 -

Y = 0.002181X + 3.1926942

RB


50 - -
DR-2

E

O                                                              HMC
25--	DR-1    RC


0	20,000	40,000	60,000	80,000	100,000




0	20,000	40,000	60,000	80,000	100,000
Aluminum (mgtkg)
Figure 5e Copper
ALUM INUM/  LEAD I
200 --


175 -    Y=0.003363X+Z551306


150 -
+ DR-2

125 --
RB

E 100 --

 
75--

DR-3
~~~~~~~R50                             .         HMC
 MC             DR-1                           I---
25                                                                       _ _



0            20,000          40,000          60,000          80,000          100,000
Aluminum (mglkg)
Figure 5f Lead


Sediment Metals Plots for the Dog River Watershed
23


| ALUMINUM/NICKEL I
50 --


 Y=O.000o321X+5.458963
40 -








20--

+ HMC
10-- -                          DR-1 R
*. RC
DR-. -
,- + MC


0           20,000          40,000          60,000         80,000          100,000
Aluminum (mg/kg)
Figure 5g Nickel
ALUM INUM /ZINC I

400 --

350--      Y=0.0014399X+7256325          RB        DR-2

300 - -

250--

E 200--


v 50                                     RC	HMC

DR-	5              DR-1	0
100 --	MC--






0	20,000          40,000          60,000          80,000         100,000
Aluminum (mglkg)
Figure 5h Zinc


Sediment Metals Plots for the Dog River Watershed
24

Benthic Biology
Introduction

Plant and animals inhabiting streambeds, living on bay bottoms and in the
ocean depths are referred to as benthic organisms. The word benthic originates from
the Greek word bathys, meaning deep. The collection of plants and animals living on
and in the bottom of a body of water is referred to as a benthic community.
The structure of a benthic community in estuarine waters is governed by
numerous factors including dissolved oxygen, salinity, nutrient concentrations,
siltation and sediment characteristics. The study of benthic communities has become
a valuable component of monitoring strategies providing information above and
beyond that which is obtained through projects focusing only on physical and
chemical parameters (Hart and Fuller eds., 1974; Hynes, 1971 and 1972; Mason et al.,
1971; Mackenthun, 1969; Pennack, 1989; Pratt and Coler, 1976 and Wilhm, 1972).
Information about the benthic community of a watershed combined with knowledge of
the watershed's geology, hydrology, water quality and land-use practices permits the
development of more effective management plans affording a greater degree of resource
protection.
For monitoring the affects of urban development and runoff in the DRW it was
decided to concentrate resources on surveying the benthic macroinvertebrate
community. Benthic macroinvertebrates in tidally influenced watersheds are typified
by crustaceans (crabs, shrimp and amphipods), mollusks (clams and snails) and
polychaetes (sandworms and clamworms). Benthic macroinvertebrates commonly
respond to specific degradation in water quality and bottom habitats; therefore, they
are good 'indicators" of environmental quality (Hynes, 1971 and 1972; Wilhm and
Dorris, 1968).

Objective

The objective of the benthic biology program was to characterize the benthic
macroinvertebrate community of the DRW relative to stream segments and tributaries,
and evaluate the water quality and sediment chemistry for chemical and physical
factors influencing the distribution of species and diversity of the community. More
specifically the program sought to quantify abundance of individuals and species;
determine diversity and evenness at different sites in the basin and compare biological
data with water quality data, sediment chemistry data and land-use practices for
25

possible associations between dissolved oxygen, nutrients, siltation and enriched
concentrations of metals.
Considering the broad nature of the watershed study it was the intention of the
survey team to demonstrate benthic biology as a watershed assessment tool and not to
conduct an in-depth study of the taxonomy of the basin. Therefore it was decided to
limit the benthic biology program to one set of samples to be gathered in a brief period
of time (preferably one day) during moderate flow. Additional detail about the aquatic
biology of the DRW (i.e. submersed grassbeds, marshland acreage, fish stocks etc.) are
far beyond the scope of this study and will have to be provided through a
comprehensive biological survey accounting for seasonal and other factors.

Materials and Methods

Six sites were visited on February 23,1995 for collecting benthic invertebrate
specimens (Figure 4). These locations are t-he same as those sampled for sedfiment
metals with one exception, Robinson Bayou was not sampled because ita shallow
depth (<lImeter) would not permit entry by a vessel equipped with a bottomn dredge.
Sites of similar stream morphology, depth and bottom habitat were selected so
as minimize natural variability as mujch as was practical. Station depths were between
1.5 and 2.5 meters and sediments primarily were silty sands with leaf and plant
debris. The bottom of Moore Creek was noticeably more sandy (i.e., coarser grained)
and the sediments of Halls Mill Creek were more muddy (i.e., more clay fmnes) than the
other stations.
At each station three replicate benthic samples were taken with a 0.05 m2
stainless steel Ponar grab for a total area sampled of 0. 15 m2 at each station. The
contents of each sample were washed through a 0.5 mnm sieve (US #35 mesh) and all
material, debris and organisms, retained on the sieve was preserved in a 10%
formaldehyde stained with rose bengal.
Each replicate was sieved a second time in the lab to further clean the sample
of sediment. The washed samples were then placed in a white enamel pan and the
organisms picked from debris using needle-nose forceps and lighted magnifiers.
Organisms were then placed in labeled capped vials containing 95%/ ethanol for
temporary storage until they were identified.
Specimens were sorted and identified to the lowest possible identification level
(LPIL) using optical light microscopes. Identified and counted specimens were
preserved in 95% ethanol in vials labeled with the taxonomic name of the organism,
location of sample site and date collected. The following references were consulted
26

when identifying macroinvertebrate specimens: Abele and Kim (1986); Brigham,
Brigham and Gnilka (1982); Fauchald (1977); Heard (1982); Holsinger (1976); Pennack
(1989); Stimpson, Klernm and Hiltunen (1982); Hopkins, Valentine and Lutz (1989);
Simpson and Bode (1980); Uebelacker and Johnson (1984); Williams, A. (1984) and
Williams, W. (1976).
Names and abundances of species collected were entered into Microsoft ExcelTM
spreadsheets for calculation of population statistics. Population statistics employed
for the benthic biology survey included the indices of community diversity, species
evenness and species richness.
These population statistics provide numerical indices which, in conjunction
with information on the types and numbers of species collected and water quality data,
allow for determination of the health of aquatic environments (Shannon and Weaver,
1963; Lloyd, et al., 1968; Margelef, 1958 and 1968; Pielou, 1975; Wilhm and Dorris,
1968).
Community diversity was calculated using the Shannon-Wiener information
measure or the Shannon index of general diversity (HI (Shannon and Weaver, 1963;
Margelef, 1968 and Pielou, 1975). The Shannon index was utilized because it
incorporates both richness and evenness. The index is calculated by the equation:

H' = -Fpi log pi
H' = the symbol for diversity in a community
pi = the proportion of the community made up by a particular species (i)
log pi = the logarithm of pi; it may be base 2, e or 10, in this study base
2 is utilized.

Species evenness was determined by Pielou's evenness index (J) (Pielou, 1966)
as calculated from:

J' H'/log s
where s = the number of species per site
H' = the Shannon-Wiener index.
27

Margelefs richness index (d) (Margelef 1958) was utilized as another measure
of health of the benthic community. This is determined by the formula:

d= s-1 /log N
where s = the number of species
N = the number of individuals per site.

Results

A total of 35 species representing 11 taxonomic classes were collected from the
six stations. The most abundant organisms were oligochaetes (Family Tubificidae),
polychaetes (Families Spionidae and Ampheretidae), larval midge flies (Family
Chironomidae) and amphipod crustaceans (Family Gammaridae). A summary of
benthic community statistics is listed in Table 3. Graphical illustrations of
abundances and diversity are shown in Figures 6a-6c. A complete listing of species
collected may be found in Table 4 and site specific information may be found in Tables
5a-5f.
The sites in Rabbit Creek (station RC) and lower Dog River (station DR- 1)
contained the most number of species (18) whereas Moore Creek (station MC)
contained the fewest (4).



TABLE 3

i-~-':'-':..............................................................'....
:::: ::: ::::: :::::: ::::::::: :: :: :: :. ' R: . :.. .: :::.......... :. :. : . : . : :....... :  : . :. :: -:.


NUMBER OF	NUMBER OF
SPEaMENS	SPEaIES	DENSIIY PER	SHANNON-WEINER	MARGELEFS   FELOUS
STAION	COLlECIED	COLLECIED	SQUARE METER	DIVERSITIY INDEX	RICHNESS INDEX EVENNESS INDEX
DR-1	489	18	3,262	2.41	6.32	0.58
DR-2	244	17	1,627	2.53	6.70	0.62
DR-3	775	14	5,169	0.96	4.50	0.25
HMC	15	6	100	1.87	4.25	0.72
MC	589	4	3,929	0.33	1.08	0.17
RC	399	18	2,661	2.79	6.54	0.67
28

The benthic communities found in Rabbit Creek (RC) and the lower Dog River
(stations DR- I and DR-2) were typical of tidally influenced soft-bottom streams. These
sites possessed a fairly good assortment of polychaete worms, aquatic insects and
amphipods normally expected to occur in such habitats. These species are, out of
necessity, tolerant of a variable environment affected by tidal flucuations, changeable
salinity, low DO concentration and other stressful forces of nature (Hudson et al.,
1990; Hynes, 1971; Dauer, 1984; Pennack, 1989 and Uebelacker and Johnson, 1984).
However, the low number of mollusks (clams and snails) at these sites is worth
note. These animals are sensitive to low concentrations of DO (Pennack, 1989) and
elevated concentrations of heavy metals, in particular copper and zinc (Becker et al.,
1990; Chapman, 1987 and Long & Morgan, 1990). Waters with a tendency to stratify
and become hypoxic are likely to have few mollusks in the benthic community; this
stress is only exacerbated by the presence of high concentrations of heavy metals in
sediments.
-----,~~~~~~~~~~~- ..................................
...........





... .. ...........
.....           ....

..........
















































 






. .


. . .


.... ... ..





...............























1
t













I



i

DoG'RivERwA:rERsFi'ED ................

::::::::::::::::::::::::::..... ..............................................
............DOG  RIVER WATERSHED.
BENTHIC INFAUNAL ABUNDANCES .





.   . .R. .....




, ,J .........

ii !iii
.fi i iOi
U.'



g~ 3,000-



m:
2 ,: :
. . .. . . . .
..
a:    ,0o
--
.m
-



E    :  X E   f     :              ~:      :
ï¿½--       :: I	I
:!	S i:: :;	:0 f0	L:C:: 0	0	IS:X	t:i	:	::0                                                                 :
W: 0	|i	iS	0:0i0t	L	T	X	:	~~I-SI	0	4:    :
:X::f:4:::: -: :S:	f:	:	fA:i:#:j:t::
H?	f0	S	00fff$	f	X	E:f	:::Sf	S	fSSSS       Sff	Sf:S	040	f	}S;
	:::ff  ff	ff	i	tt	;f	ftt:fS	:	'         $             :


\f::	t; ifS il	t	; i	0i1002000 ttX0	i;	i
RG 777
..... '.....
.......................................................................................
~~~~~~~~~~~............    ,,,,I
~~~~~~~~..... .......... ........ . . . . . . . . . . . . . . . . . . . . . . . .                                                  . . . . . . . . . .
~~~~~................. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
~~~~~~~~~~~~~............. .............,......,.
~~~~................ ......... . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
I............................................................................................  I   ~I~                                                                   II   I:.   i        I  :
... ... ... ... ... ... ... ... ... ... ... ... ... ... ...                                     ........         ...... ..... ..... ....
Figure 6a
29

:DOG RIVER WATERSHEDj
BENTHIC TAXA


20 - -- --










mLU








DR-1      DR-2      DR-3       HMC        Mc        RC
STATION
Figure 6b
DOG RIVER WATERSHED
BENTHIC COMMUNITY DIVERSITYj






x.' 2.5
z                W
2.10 -5 p



LU2z0	1	-



DR-1     DR-2     DR-3	HMC      Mc	RC
STATION
Fligu-re 6c
30

Shannon-Wiener diversity index values were 2.79 for station RC, 2.41 for
station DR-i1 and 2.53 for station DR-2. Previous studies of the benthic communities
of coastal Alabama (ADEM-FDER, 199 1; Marine Environmental Corsortium, 1981 and
US Army Corps of Engineers, 1978) indicate that these values are representative of the
area's shallow, soft-bottom tidal streams. The values of the other diversity measures
(Margelefs richness and Pielou's evenness) also are in line with the findings of those
sttxdies.
Considering the naturad variability of tidally influenced streams in conjunction
with characteristics and abundances of the species collected, the benthic communities
of Rabbit Creek and the lower Dog River appear to be fairly representative of gulf coast
small streams.
As previously stated, inhabitats of these waters are frequently exposed to
various stressful forces of natuxre. For local estuaries these stresses take the form of
highly variable salinity and low DO concentration. Nonetheless, urban development
and other anthropogernie activities exert addhtional stresses on waterboches and their
inhabitants. The effects of these disturbances often are expressed in the species and
number of individuals present in the sediments of these waters.
The benthic invertebrate data for the sites on Hals Mill Creek (station H MC),
Moore Creek (station MC) and upper Dog River/lower Eslava Creek (DR-3) illustrate
this situation. The communities at these sites show the effects of erosion, urban
runoff and other factors related to development.
The extremely low number of individuals (only 15 specimens) from the Halls
Mill Creek site is considered by aquatic biologists to be an indication of a disturbance,
such as siltation, with broad effects to the entire infaunal community (Hynes, 1971
and Pennack, 1989). The Moore Creek and upper Dog River sites possessed good
numbers of individuals (589 and 775 respectively) but over 90% of the specimens were
oligochaetes, primarily tubificids.
Oligochaetes are among the most pollution tolerant organisms inhabiting
aquatic environments. They are exceptionally adept at surviving prolonged periods of
extremely low DO, organic enrichment and high concentrations of heavy metals. Their
abundance, coinciding with a near absence of other taxonomic groups, is a reliable
indicator of polluted waters (Chapman et al., 1979; Hynes, 1971 and 1972; Hart and
Fuller, 1974; Stimpson, Klemm and Hiltunen 1982; and Pennack, 1989).
Additional evidence of the damage done to the aquatic habitats of Halls Mil
Creek, Moore Creek and upper Dog River/lower Eslava Creek is presented by the
numerical indices. Values of the Shannon diversity index less than I for local benthic
31

communities indicate the presence of stress above and beyond that normally expected.
The diversity values for the Moore Creek site (H'=0.33) and the upper Dog River/lower
Eslava Creek site (H'-0.96) are exceptionally low compared to values from studies of
other local streams and estuaries (ADEM-FDER, 199 1; Marine Environmental
Corsortium, 198 1; Geological Survey of Alabama, 1983).
These findings together with the data on sediment chemistry and water quality
show that Moore Creek, Halls Mill Creek and the upper section of Dog River have been
severely affected by land development and other anthropogenic activities. Rabbit
Creek and the middle and lower reaches of Dog River possess fairly diver-se and
productive habitats but these appear to show some signs of the factors affecting the
other sites. The more pronounced effects observed in Moore Creek, Halls Mills Creek
and at the upper Dog River station are probably a consequence of their closer
proximity to developmental activities.
32

TABLE 4
LIST OF BENTHIC INVERTEBRATE SPECIES COLLECTED FROM THE
DOG RIVER WATERSHED

PORIFERA(LPIL)
HYDROZOA
Hydridae
Hydra americana
NEMERTEA (LPIL)
NEMATODA (LPIL
OLIGOCHAETA
Tubificidae
Ilyodrilus templetoni
Limnodrilus daparedianus
Limnodrilus cervix
Spirosperma ferox
Branchiura sowerby
POLYCHAETA
Amphaeretidae
Amphectis gunneri
Hobsoniaflorida
Nereidae
Laeonereis culveri
Neanthes micromma
Capitellidae
Mediomastus ambeseta
Spionidae
Streblospio benedicti
Polydora cornuta
Pilargidae
Parandalia americana
HIRUDINEA
Glossiphoniidae
Placobdella ornata
INSECTA
Diptera
Chironomidae
Coelotanypus scapularis
Chironomus stagenri
Clinotanypus pinguis
Cryptochironomus fulvus
Glyptotendipes meridionalis
Procdadius bellus
Dicrotendipes neomodestus
Ceratopogonidae
Bezzia/ Probezzia sp
33

TABLE 4 cont.
INSECTA
Ephemeroptera
Caenidae
Caenis diminuta
Baetidae
Baetis (LPIL)
AMPHIPODA
Corophidae
Corophium louisianum
Aoridae
Grandierellia bonnieroides
Gammaridae
Gammarus mucronatus
MYSIDACEA
Mysidae
Bowmanella floridana
PELECYPODA
Mactridae
Rangia cuneata
Mulinia ponchartrainensis
Tellinidae (LPIL)
34

TABLE 5A
...	.       ~        ~	~      ,......................... I........... .....  ............... ..............

PHYLUM	CLASS	FAMILY	SPECIES -TAXON(LPIL)           NUMBER
COELENTERATA	HYDROZOA	HYDRIDAE	Hydra americana	2
NEMATODA	NEMATODA (LPIL)	1
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	Ryodrilus templetoni	30
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	Limnodrilus claparedianus	68
ANNELIDA	POLYCHAETEA	AMPHARETIDAE	Hobsoniaflorida	108
ANNELIDA	POLYCHAETEA	NEREIDAE	Neanthes micommma	2
ANNELIDA	POLYCHAETEA	SPIONIDAE	Streblospio benedicti	1
ANNELIDA	POLYCHAETEA	SPIONIDAE	Polydora cornuta	1
ARTHROPODA	INSECTA	CAENIDAE	Caenis diminuta	1
ARTHROPODA	INSECTA	CERATOPOGONIDAE	Bezzia/Probezzia sp	1
ARTHROPODA	INSECTA	CHIRONOMIDAE	Procadius bellus	10
ARTHROPODA	INSECTA	CHIRONOMIDAE	Di/rotendipes neomodestus	6
ARTHROPODA	CRUSTACEA (AMPHIPODA)	COROPHIIDAE	Corophium louisianum	34
ARTHROPODA	CRUSTACEA (AMPHIPODA)	AORIDAE	Grandierellia bonnieroides	101
ARTHROPODA	CRUSTACEA (AMPHIPODA)	GAMMARIDAE	Gammarus mucronatus	30
ARTHROPODA	CRUSTACEA (MYSIDACEA)	MYSIDAE	Bowmanellafloridana	1
MOLLUSCA	PELYCEPODA	MACTRIDAE	Rangia cuneata	1
MOLLUSCA	PELYCEPODA	MACTRIDAE	Muliniaponchartrainensis	1

NUMBER OF INDIVIDUALS	399

DENSITY PER SQUARE METER	2661
NUMBER OF SPECIES	18
SHANNON-WEINER INDEX	2.79
MARGELEF'S RICHNESS INDEX	6.54
PIELOU'S EVENNESS INDEX	0.67




TABLE 5B
....-....... ..........................................................................-.:.:.ï¿½.... ........-.l:...-...............:
.DOG. RIVERWATERSHED  EFITHIQ INAUA. :DATA. ~fAU..sJOLL-CREEK SATO

PHYLUM	CLASS	FAMILY	SPECIES- TAXON(LPIL)              NUMBER

ANNELIDA	OLIGOCHAETA	TUJBIPICIDAE	Limnodridus oertix	9
ANNELIDA	POLYCHAETA	AMPHARETIDAE	Hobsoniaflorida	1
ANNELIDA	POLYCHAETA	AMPHARETIDAE	Amphectis gunneri	1
ANNELIDA	POLYCHAETA	SPIONIDAE	Streblospio benedicti	2
ARTHROPODA	INSECTA	CHIRONOMIDAE	Chironomus stagei	1
ARTHROPODA	INSECTA	CHIRONOMIDAE	Procladius belfts	1
I


N






I
Y

NUMBER OF INDIVIDUALS	15

)ENSITY PER SQUARE METER	100
NUMBER OF SPECIES	6
SHANNON-WEINER INDEX	1.87
MIARGELE'S RICHNESS INDEX	4.25
PIELOUS EVENNESS INDEX	0.72
35

TABLE 5C
.::                    R: i::  .	. :  : : :: ::: ::: :: :: :::::::: :: : :::::::: : :::::
PHYLUM           CLASS                    FAMILY	SPECIES - TAXON(LPIL)           NUMBER
PORIFERA	PORIFERA(LPIL)	2
NEMERTEA	NEMERTEA(LPIL)	5
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	'UBIFICIDAE (LPIL)-IMMATURE	13
ANNELIDA	POLYCHAETA	AMPHARE'TIDAE	Hobsoniaflorida	192
ANNELIDA	POLYCHAETA	CAPITELLIDAE	Mediomastus ambeseta	127
ANNELIDA	POLYCHAETA	PILARGIDAE	Parandalia americana	1
ANNELIDA	POLYCHAETA	SPIONIDAE	Streblospio benedicti	94
ARTHROPODA	CRUSTACEA (AMPHIPODAj	AORIDAE	Grandidierella bonnieroides	21
ARTHROPODA	CRUSTACEA (AMPHIPODA)	COROPHIIDAE	Corophium louisianum	5
AR'THROPODA	CRUSTACEA (AMPHIPODA)	GAMMARIDAE	Gammanus mucmonatus	1
ARTHROPODA	CRUSTACEA (MYSIDACEA)	MYSIDAE	Bowmanellafloridana	1
ARTIIHROPODA	INSECTA	CHIRONOMIDAE	Chironomus staged	7
AR'IHROPODA	INSECTA	CHIRONOMIDAE	Prodadius bellus	9
ARTHROPODA	INSECTA	CHIRONOMIDAE	Dichrotendipes neomodestus	4
ARTHROPODA	INSECTA	CHIRONOMIDAE	Clinotanypuspinguis	4
ARTHROPODA	INSECTA	CHIRONOMIDAE	Cjryptochironomus fuluus	1
MOLLUSCA	PELECYPODA	MACTRIDAE	Rangia cuneata	I
MOLLUSCA	PELECYPODA	MACTRIDAE	Muliniaponchartrainensis	1

NUMBER OF INDIVIDUALS	489
DENSITY PER SQUARE METER	3262
NUMBER OF SPECIES	18
SHANNON-WEINER INDEX	2.41
MARGELEFPS RICHNESS INDEX	6.32
PIELOU'S EVENNESS INDEX	0.58




TABLE 5D
- - -..-.- .-.. . . . .. ..........-.-  .-.........................................................
.....IER  WA.RSHED	T.PHAUMA ................CS'   FMOIY S ECREEKS -TATIN(L:

PHYLUM	CLASS	FAMILY	SPECIES- TAXON(LPIL)            NUMBER
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	Limrodrus cparedanus	556
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	Brawchia sowerby	1
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	lbyodrls lerpleWoni	31
ANNELIDA	POLYCHAETA	AMPHARETIDAE	Hobsoni brida	1

N

I
D




I
V
p

NUMBER OF INDIVIDUALS	589

DENSITY PER SQUARE METER	3929
NUMBER OF SPECIES	4
SHANNON-WEINER INDEX	0.33
MARGELEFS RICHNESS INDEX	1.08
PIELOU'S EVENNESS INDEX	0.17
36

TABLE 5E
DOG RIVER WATERSHED RENThJQ REAUN~~~~AL:DAT.  -TA-- 'N:D-

PHYLUM          CLASS                   FAMILY	SPECIES-TAXON(LPIL)            NUMBER
NEMATODA	NEMATODA (LPIL)	1
NEMERTEA	NEMERTEA (LPIL)	3
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	Tlyodrilus templetoni	3
ANNELIDA	OLIGOCHAETA	TUBIFICIDAE	Limnadrilus cdaparedianus	10
ANNELIDA	POLYCHAETA	AMPHAREIIDAE	Hobsoniaflorida	118
ANNELIDA	POLYCHAETA	NEREIDAE	Laeonereis culveri	1
ANNELIDA	POLYCHAETA	CAPITELI DAE	Mediomastus ambeseta	36
ANNELIDA	POLYCHAETA	SPION1DAE	Streblospio benedicti	19
ARTHROPODA	INSECTA	CHIRONOMIDAE	Chironomus staged	16
ARTHROPODA	INSECTA	CHIRONOMIDAE	Procladius bellus	3
ARTUROPODA	INSECTA	CHIRONOMIDAE	Cainotan_puspinguis	2
ARTHROPODA	INSECTA	CHIRONOMIDAE	Cngptohimronomusfiuluus	1
ARTHROPODA	INSECTA	BAETIIDAE	Baetis (LPIL)	1
ARTHROPODA	CRUSTACEA (AMPHIPODA)	AORIDAE	Grandidierella bonnieroides	26
ARTHROPODA	CRUSTACEA (AMPHIPODA)	COROPHIIDAE	Corophium louisianum	2
ARTHROPODA	CRUSTACEA (MYSIDACEA)	MYSIDAE	Bowmanellafloridana	1
MOLLUSCA	PELECYPODA	TELIUNIDAE	TELLINIDAE (LPIL)	1

NUMBER OFINDIVIDUALS	244

DENSITY PER SQUARE METER	1627
NUMBER OF SPECIES	17
SHANNON-WEINER INDEX	2.53
MARGELEF'S RICHNESS INDEX	6.70
PIELOU'S EVENNESS INDEX	0.62


TABLE 5F
.2 QQQ RIVER WATERSHED DENT$1C INF                 DATA-STATiON: DR-8  ::::
PHYLUM           CLASS                    FAMILY               SPECIES-TAXON(LPIL)             NUMBER
ANNELIDA
ANNELIDA
ANNELIDA
ANNELIDA
ANNELIDA
ANNELIDA
ANNELIDA
ARTHROPODA
ARTHROPODA
ARTHROPODA
ARTHROPODA
ARTHROPODA
ARTHROPODA
MOLLUSCA
1
79
2
649
2
5
2
2
21
2
5
3
1
1
OLIGOCHAETA
OLI GOCHAETA
OLIGOCHAETA
OLIGOCHAETA
HIRUDINEA
POLYCHAETA
POLYCHAETA
CRUSTACEA (MYSIDACEA)
INSECTA
INSECTA
INSECTA
INSECTA
INSECTA
PELECYPODA
TUBIFICIDAE
"UBIFICIDAE
TUBIFICIDAE
ItBI F CIDAE
GLOSSIPHONIIDAE
AMPHARE'TIDAE
NEREIDAE
MYSIDAE
CHIRONOMIDAE
CHIRONOMIDAE
CHIRONOMIDAE
CHIRONOMIDAE
CHIRONOMIDAE
MACTRIDAE
Branchiura sowerby
Ilyodrilus templetoni
Spirospermaferox
Limnodrilus claparedianus
Placo bdella omnata
Hlobsonia florida
Laeonereis culueri
Bow manellafloridana
Procladius bellus
Coelotan_pus scpularis
Cryptochim ronomus fiulvus
Clinotanrpus pinguis
Gl_ptotendipes meridionalis
Pangia cn,natfa

N

D
N
S
m
P
"'~_-__

tUMBER OF INDIVIDUALS	775

)ENSITY PER SQUARE ME'ITER	5169
UMBER OF SPECIES	14
HANNON-WEINER INDEX	0.96
IARGELEF'S RICHNESS INDEX	4.50
IELOU'S EVENNESS INDEX	0.25
37

Review and Conclusiond
The impacts of land use patterns and their related non-point sources on the
waters of the DRW are clearly evident fromn the results of this survey. Dog River and its
tributaries receive nminimal amounts of wastewater from point sources; however,
turbidity values, nutrient concentrations, enteric bacteria densities and metallic
enrichment of sediments were observed to be as greatly elevaLted, if not more, as these
parameters are in streams receiving significant discharges of effluent from municipal
and/or industrial facilities.
The specific impacts affecting a given tributary of the DRW appear to be highly
characteristic of the land use witbin the individual sub-basin. Such associations of
land use and umpacts on water quality and sediment chemistry have been observed
during similar studies of the impacts of non-point sources on watersheds (National
Oceanic and Atmospheric Administration 1989; National Research Council 1990; U.S.
Environmental Protection Agency 199 1).
The land-use practices which appear to most significantly affect the basin are
locating developments on soils with poor drainage characteristics, draining and filling of
wetlands, channelization of streams, streets and parlking lots not kept clean of trash and
other debris, residences with septic tanks located in low lying areas near streams, poor
erosion control practices during construction activities, lawn and golf course
maintenance and in general, increasingly large areas of impervious cover forcing greater
volumes of storm water runoff into heavily loaded drainage courses. Additionally, there
appears to be a source of enteric bacteria (either undiscovered sewer line breaks or
sanitary line ties to storm sewers) for the streams drainiing urbanized areas.
The findings of this survey will be put to use with the recently implemented
NPDES General Permit program for controlling stormwater runoff at construction sites
and also the Mobile Standard Metropolitan Statistical Area stormwater permit. The
permit requirements for controlling runoff and erosion with construction site BMP's
should, if properly maintained, provide a significant reduction in the suspended solids
loads and turbidity of area streams. This will in turn provide a chance for aquatic
habitats and communities to reestablish in the watershed.
The Mobile Area Water and Sewer Service has increased its inspection and
maintenance of sanitary lines operated by MAWSS. The task facing the MAWSS is a
formidable one since the routes of many sewer lines in the older neighborhoods of
Mobile are incompletely known. This situation is further complicated from numerous
tie-ins of sanaitary lines to storm sewers in the downtown area. There also is the
38

problem of improper installation and connection practices of sewers in some
subdivisions and private developments. Not only do these defective systems contribute
to the degradation of surface waters but repair and replacement of faulty components
consumes resources of the MAWSS which might be devoted to other operations. At the
time this report was in preparation the MAWSS had made considerable progress
locating problems and taking corrective measures to eliminate discharges of untreated
sewage to local waters.
The problems observed with excessive concentrations of metallic elements in
sediments will, hopefully, diminish as requirements for control of urban stormwater
runoff and industrial facility runoff go into effect. Additional decreases of these
pollutants also should be realized through the elimination of lead from gasoline and
paint, the prohibition of organo-tin compounds in marine paints and other controls
placed on the use of toxic substances in paints and wood treatments.
Lastly, the trash and litter problem (primarily plastics) that is so pervasive along
Eslava Creek and Dog River will be solved only through the efforts of the citizens living
and working in the DRW. The acceptance of civic responsibility on the behalf of all
citizens and the realization that trash in a parking lot or a curbside gutter will end up in
the local waterways and along the shorelines will accomplish as much to improve the
quality of the Dog River Watershed as the permitting and control programs.
39

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45