synthesis of water quality and contaminants data for the white perch, morone americana : final draft

[From the U.S. Government Printing Office, www.gpo.gov]

A SYNTHESIS OF WATER QUALITY AND
CONTAMINANTS DATA FOR WHITE
PERCH, MORONE AMERICANA
FINAL DRAFT Sep, 1989

COASTAL ZOKEB'-'

INFORNIATION

SH
171
.S96
1989

FINAL DRAFT

A SYNTHESIS OF WATER QUALITY AND CONTAMINANTS DATA FOR
WHITE PERCH, MORONE AMERICANA

Steven A. Fischer
Lenwood W. Hall, Jr.
and
John A. Sullivan

The Johns Hopkins University
Applied Physics Laboratory
Aquatic Ecology Section
shady Side, Maryland

COAST LT- ZONE

INFO-@@...@4 ji. i 03N CENTER

September, 1989

Preparation of this report was funded by the Coastal Resources
Division, Tidewater Administration, Maryland Department of Natural
Resources, through a CZM Program Implementation Grant from the
Office of Ocean and Coastal Resource Management, NOAA.
MD W. P.11

DRAFT

INTRODUCTION

The Chesapeake Bay, with its' unique physical, chemical and

biological characteristics, creates a suitable environment for

numerous fish species. The abundance and distribution of

resident and migratory fish species which utilize the Bay, as

well as the recruitment potential of estuarine-reared oceanic

fish species, are influenced by variables such as climate,

reproductive potential, parasites, disease, natural population

cycles, food availability and suitable habitat. Habitat

degradation (water quality and contaminant) and overharvesting of

prized commercial and recreational fish species are the primary

causes of dramatic and prolonged fish stock declines (Wohlfarth,

1986; Setzler-Hamilton, 1987; Speir, 1987). Habitat loss,

resulting from adverse water quality and chemical contaminants,

has recently been suspected in reducing several Chesapeake Bay

fish species populations (Hendrey, 1987; Klauda and Bender,

1987).

Deterioration of spawning and nursery habitats of fish

species in Chesapeake Bay is a serious consideration when

attempting to manage a species. Populations of anadromous and

resident fish species, including the white perch (Morone

americana), have drastically declined in recent years (Hendrey,

1987; Klauda and Bender, 1987; Speir, 1987). White perch are

classified as freshwater to oligohaline (0.0 - 4.0 ppt) spawners

within tributaries of the Bay (Hardy 1978). Larval and juvenile

white perch are also inhabitants of freshwater and oligohaline

DRAFT

environments. The early life history of white perch results in

the exposure of eggs, larvae and juveniles to potentially toxic

conditions present within the Chesapeake Bay and associated

tributaries. Efforts should be increased in an attempt to

identify adverse conditions associated with the reduction of

white perch if adequate management plans are to be implemented in

the future. Synthesis of the data can also be used to identify

suitable habitat requirements.

This document was developed to provide a compilation and

review of both water quality and contaminants data on various

life stages of white perch. Data contained in this document will

be useful in the Toxics Reduction Strategy for the Chesapeake Bay

Program effort. A life history and ecology section on white

perch will be prepared by other investigators and merged with

this document to provide a complete review on the species.

TOXIC WATER QUALITY CONDITIONS

Toxic water quality conditions adversely affecting various

life stages of white perch are presented in Table 1. Each

parameter is discussed separately in the following sections.

Temperature

The effects of temperature on white perch eggs were

examined in five different studies. The optimum temperature for

AFI

white perch egg hatching was 14.1 C at a salinity of 0 ppt

(Morgan and Rasin, 1982). Hardy (1978) indicated that hatching

occurred in 24 h between 16 - 20 C, while 144 h were required

between 11 - 16 C. ,Hardy (1978) also reported ambient water

temperatures below 10 C caused significant mortality, while

Ecological Analysts (1978) reported normal hatching occurred at

30.5 C. AuClair (1960) and Hardy (1978) reported that

temperature drops of 4 - 5 C were lethal to developing eggs,

while sudden drops of 2 - 3 C were sufficient to cause egg

mortality. No significant effect on hatching success was

observed when white perch eggs, acclimated at 13.5 - 14.5 C, were

exposed to temperature increases of 6 - 10 C for < 1 h (Schubel,

1974).

Two studies have evaluated the effects of temperature on

larval white perch. Maximum length of white perch larva at

hatch occurred at 18 C when acclimated over a temperature range

of 8 - 26 C (Morgan and Rasin, 1982). Ecological Analysts (1978)

reported a 24 h TL50 range of 30.2 - 31.8 C when acclimated at

24 C.

Temperature effects on juvenile white perch were examined in

four different studies. Ecological Analysts (1978) reported that

YOY white perch exhibited a preferred temperature of 31.2 C when

acclimated at 24 C. Hall et al. (1979) reported that juveniles

acclimated between 6 - 33 C exhibited final temperature

preferences between 15.2 - 31.0 C. A 14 d TL50 temperature of

33.8 C, and a 96 h TL50 temperature range of 32.4 - 34.7 C, were

'0" R A F T

reported for early juveniles acclimated to 24 C (Ecological

Analysts, 1978). Dorfman and Westman (1970) indicated 80%

survival of juveniles exposed to 30.6 C for 24 h after exposure

for three days to increasing temperatures beginning at 20 C.

They also reported a critical thermal maximum (CTM) temperature

of 36.4 C, which was dependent upon acclimation temperature.

Marcy (1976) collected young-of-the-year (YOY) white perch in

water ranging from 5.7 - 40 C.

Ten studies have examined the effects of temperature on

adult white perch. Terpin et al. (1977) utilizied vertical

temperature preference studies to determine final temperature

preferences of adult white perch. They reported that adults

acclimated at 5, 8 and 10 C in 26.5 - 27 ppt salinity preferred

23, 22.8 and 21.5 C, respectively. A summer maximum preferred

temperature of 32.2 C for adult perch in 4 - 9 ppt salinity from

the Delaware River was reported by Meldrim and Gift (1971). A

preferred temperature of 27.8 C was exhibited by adult white

perch from the Hudson River (Ecological Analysts, 1978). Hall

et al. (1978) reported that significant differences existed in

final temperature preferenda amoung age-O white perch populations

from North Carolina, Maryland, and New Jersey. Adult white perch

from the Hudson River avoided temperatures < 9.5C and > 34.5 C

(Texas Instruments, 1976), while an upper avoidance temperature

of 32 C was reported for adult perch in New Jersey Bay (Gift and

Westman, 1971). McErlean and Brinkley (1971), Meldrim and Gift

(1971),.Meldrim et al. (1974) and PSE&G (1978) reported that

-'m n
UKAFT

upper lethal temperatures varied as a result of acclimation

temperatures. Texas Instruments (1976) and Ecological Analysts

(1978) reported a 96 h LC50-range of 32 - 35 C for adult white.

perch. Gift and Westman (1971) reported a CTM temperature of

37.6 C. Exposure to a temperature increase of > 9 C for > 15 min

caused mortality in adult white perch acclimated to temperatures

between 15.5 - 26.7 C (Meldrim and Gift, 1971), while a 20 C

decrease in temperature resulted in total mortality for adults

acclimated to 26 C (PSE&G, 1978). Burton (1979) indicated adult

white perch ventilation rates increased with increased ambient

temperature. Meldrim et al. (1974) determined that temperature,

and not salinity or body length, contributed significantly to

estimates of active and inactive metabolism in adult white perch.

Salinity

Few studies have examined the effects of salinity on various

life stages of white perch. Only one experiment examined the

effect of salinity on white perch eggs. Morgan and Rasin (1982)

indicated that mean egg diameter was inversely related to

salinity. They also reported eggs tolerate a salinity range of 0

10 ppt when exposed to temperatures of 8 - 26 C.

White perch larvae and juveniles inhabited a salinity range

of 0 - 8 ppt, while the majority of larvae and juveniles

preferred salinities < 1.5 ppt and < 3 ppt, respectively (Stanley

and Danie, 1983). Both larval and juvenile white perch life

R A F T

stages have been collected in waters with up to 13 ppt salinity

(Stanley and Danie, 1983).

A normal salinity range for adults of 5 18 ppt was

reported in Stanley and Danie (1983). It was also reported that

spawning occurs at salinities < 4.2 ppt (Hardy, 1978).

Dissolved Oxygen

only two studies have examined the effects of low dissolved

oxygen (D.O.) on white perch YOY and adults. Dorfman and Westman
(19-70) reported 60% survival for YOY white perch when exposed to

D.O. concentrations of 0.5 - 1.0 mg/L for 19 h over a

temperature range of 6.7 - 28.3 C. Adult white perch avoided

waters with < 35% saturation of oxygen over a temperature range

of 8 - 21 C (Meldrim et al., 1974).

A paucity of information exists concerning the effects of pH

on various life stages of white perch. Klauda (1989) reported

that laboratory and field data concerning the tolerance of white

perch early life stages was lacking. However, he proposed that

reproductive success of white perch would be significantly

reduced if an acid pulse of pH 6.5 - 6.7, in association with a

total monomeric aluminum concentration of 25 ug/L and dissolved

calcium levels of 2 mg/L, continued for 7 d. Klauda (1989) also

DRAFT

suggested that short duration 48 h) acidic pulses to pH 6.0

could severly impact survival of white perch larvae. Stanley and

Danie (1983) assumed that adult white perch tolerate a pH range

of 6.0 - 9.0.

Suspended Solids

The effects of suspended solids on white perch eggs were

examined in four studies. Morgan et al. (1983) reported that

hatching success was not significantly affected when eggs were

exposed for 12 h to concentrations < 5250 mg/L, however, ha tching

was delayed 24 h at a concentration of 5250 mg/L. Schubel and

Wang (1973) reported suspended sediment concentrations as low as

100 and 500 mg/L caused hatching delays of 4 - 6 h. Auld and

Schubel (1974), using unreplicated data, reported continuous

exposure at a concentration of 1000 mg/L natural fine-grained

sediment significantly reduced hatching success. It was reported

in Schubel et al. (1977) that deposition of sediment on white

perch eggs was more important than suspended sediment

concentration. They reported 100% mortality when eggs were

covered with a 1.1 mm layer of sediment on top of the eggs.

They also reported no significant reduction in hatching success

when a sediment layer (0.45 mm) less than one-half egg diameter

was deposited around eggs.

Two studies were conducted on the deleterious effects of

suspended solids to white perch larvae. Morgan et al. (1973,

'DRAFT

1983) reported.24 h and 48 h LC50 values of 67,000 mg/L and 6,900

mg/L, respectively.

only one study examined the effects of suspended sediments

on juvenile white perch. Auld and Schubel (1974) indicated that

concentrations of suspended solids > 500 mg/L significantly

reduced survival of juvenile white perch.

McInnich and Hocutt (1987) examined the response of adult

white perch to strobe lights and bubble curtains in varying

levels of turbidity. They reported only 40% avoidance to strobe

lights at high turbidity,(102 - 138 NTU). White perch avoided

bubble curtains at low turbidity (45 NTU) but were attracted in

clear and high turbidity conditions.

Shear

The effects of shear forces on white perch eggs and larvae

were investigated in one study. Morgan et al. (1976) stated that

shear stress can cause mortality of eggs and larvae by creating

excess rotation or deformation. They reported that LS50 (median

lethal shear that would kill 50% of test animals in a given time

period) values calculated from time-shear exposure experiments

were much greater than those present within the Chesapeake and

Delaware canal. They also indicated the magnitude of shear force

required to cause significant mortality is only present within a

very thin boundary layer (20 mm).

DRA

TOXICITY TO SINGLE CONTAMINANTS

Toxicity data for white perch egg, larval and adult life

stages exposed to nine different single chemicals are presented

in Table 2. Two studies have examined the deleterious effects of

total residual chlorine (TRC) on white perch eggs. Morgan and

Prince (1977) reported a 76 h LC50 value of 0.27 mg/L TRC for

white perch eggs maintained at 15 C in 2.5 ppt salinity. Later,

Morgan and Prince (1978) reported that egg development ceased at

the early embryo stage when exposed to 0.55 mg/L TRC at 15 C in

2.5 ppt salinity.

Six studies examined the effects of larval white perch

exposed to chlorine. When comparing chlorine toxicity data, the

terms total residual chlorine (TRC), chlorine produced oxidants

(CPO), and total residual oxidants (TRO) are equivalent. A 24 h

LC50 value of 0.31 mg/L TRC for white perch larvae maintained at

15 C in 2.5 ppt salinity was reported by Morgan and Prince

(1977). In another study, Morgan and Prince (1978) indicated

that length of larvae at hatch decreased with increasing TRC

concentrations, and reported that length of larvae at hatch was

significantly less (2.5 - 5.5%) than the length of control larvae

at concentrations > 0.10 mg/L TRC. Burton et al. (1979), and

Hall et al. (1979; 1983) reported that mortality of larval white

perch was a function of TRC and exposure duration. They also

reported that temperature changes < 10 C above an acclimation

temperature of 18 C in 0.5 - 2.5 ppt salinity for < 4 h did not

11 '
URAFT

affect survival of larval white perch. Hall et al. (1981) later

reported that larvae acclimated at 23 C exhibited greater

mortality at all treatment conditions than larvae acclimated at

15 C. They concluded the changing temperature effect resulted

from an increased observation period (36 - 96 h).

Rehwolt et al. (1971) examined the effects of three heavy

metal ions to adult white perch acclimated at 17 C. Adult perch

were twice as sensitive to copper (96 h TL50 = 6.2 mg/L) as they

were to either nickel or zinc (96 h TL50 = 13.6 and 14.3 mg/L,

respectively).

Rehwolt et al. (1974) examined the toxic effects of No. 2

and 4 fuel oils, an oil collection agent, a dispersant, and

mixtures of each to adult white perch. The toxicity of the

dispersant (96 h TL50 = 4.2 mg/L) was 8 - 9 times greater than

the toxicity of either fuel oil (96 h TL50 values ranged from 31

- 37 mg/L), while the oil collecting agent was not toxic to perch

(96 h TL50 > 500 mg/L). Toxicity of the fuel oils increased

greatly when the dispersant was added, which was due to partial

solubilization of the oils (96 h TL50 ranged from 1.0 - 1.4

mg/L). Fuel oil toxicities were not significantly affected by

the addition of the collecting agent.

Meldrim et al. (1981) reported that total chlorine was more

toxic to adult white perch in salt water (1 ppt) at 14.5 C than

in freshwater at 11 - 26 C. Ninety-six h LC50 values were 0.10

mg/L in saltwater and 0.61 - 0.87 mg/L in freshwater.

Conversely, ozone was more toxic to adult white perch in

D A

freshwater at 11 - 27 C (96 h LC50 = 0.22 - 0.37 mg/L) than in

saltwater (1 ppt) at 14.5 C (96 h LC50 > 0.66 mg/L). Meldrim et

al. (1981) also reported that avoidance responses and

physiographic studies (cough responses) were consistant with

trends observed in the acute toxicity experiments. A 24 h TL50

value of 2.8 mg/L total chlorine was reported by Lauers (1973)

when he exposed adult white perch to a single 2 h dose of NaOC1

under static conditions.

PSE&G (1978) reported a 96 h TL50 value of 0.22 mg/L TRC for

adult white perch acclimated at 16.7 C and 2,.7 ppt salinity, and

an avoidance concentration mean of 0.21 mg/L TRC for adult pe rch

tested at 4 - 28 C and 0 - 8 ppt salinity. Gullans (1977)

reported 96 h LC50 values for CPO of 0.21 and 0.15 mg/L for adult

white perch acclimated at 15 and 25 C, respectively. Block

(1977) and Block et al. (1977) examined the physiological effects

of CPO on adult perch in freshwater at 14 - 16 C. After 0.5 h

exposure to a concentration of 1.3 mg/L CPO, Block et al. (1977)

reported that blood pH decreased from 7.5 to 7.0, and gill

carbonic anhydrase and hematocrit increased 76% and 106%,

respectively. Block et al. (1978) also reported that in a saline

environment (13.6 ppt) blood pH decreased from 7.6 to 6.8 and

hematocrit decreased 14%.

Meldrim et al. (1974) reported an inverse relationship

between temperature and concentration of Free Residual Chlorine

(FRC) required to bring about an avoidance response by adult

white perch. A similar relationship was observed between

NAB
salinity and concentration of FRC. PSE&G (1978) indicated'that

an inverse relationship existed between the percentage of FRC in

chlorine and the concentration of total chlorine required to

bring about an avoidance response.

Meldrim and Flava (1977) examined the avoidance response of

adult white perch to TRO, and TRO with a temperature increase of

2 - 3 C, in fresh and saline waters (0 - 7 ppt) at temperatures

of 0 - 27 C. He reported adult perch were more sensitive to TRO

with a 2 - 3 C temperature change when ambient water temperatures

were 0 - 12 C. Conversely, adult perch were more sensitive to

the concentration of TRO, and less sensitive to a temperature

change, when ambient water temperatures ranged from 13 - 27 C.

Rosenkranz et al. (1978) and Richardson et al. (1983)

reported similar 96 h LC50 values (0.20 - 0.22 mg/L) of ozone

produced oxidants (OPO) for adult white perch. In both of these

studies histological changes were observed on gill surfaces

within 24 h of exposure to concentrations > 0.01 mg/L OPO. In

addition, Richardson et al. (1983) indicated that blood pH was

significantly reduced at OPO concentrations > 0.15 mg/L and that

hematocrit significantly increased when OPO concentrations > 0.10

mg/L.

Contaminated harbor water

One experiment examined the sublethal effects of chemicals

present within a, specific body of water on adult white perch

DRAFT

(Table 3). Morgan et al. (1973b) examined the sublethal"effects

of Baltimore harbor water on adult white perch by exposing them

for 30 days in 25 C harbor water at 5 ppt salinity. Sublethal

physiological effects to adult perch included increased levels of

thrombocytes, and decreased neutrophil and basolphil levels.

Biochemical effects included changes in lactate dehydrogenase

(LDH), acetylcholinesterase, and catalase levels. Increased LDH

activity in white perch blood serum was in response to poor water

quality. Organophosphorous pesticides were responsible for the

reduced acety1cholinesterase activity within white perch brains,

while liver damage from metal ions resulted in decreased catalase

levels.

CONCLUSIONS

1. Populations of white perch have dramatically declined within

the Chesapeake Bay in recent years. White perch spawn in

fresh water and oligohaline (0.5 - 4.0 ppt) tributaries of

the Bay, while larval and juvenile stages also inhabit

similar environments. Early life history stages of this

species are thus exposed to potentially toxic conditions

within the Chesapeake Bay and associated tributaries.

2. The optimum hatching temperature for white perch eggs is 14.1

C at 0 ppt salinity. Maximum length at hatch for larvae

occurred at 18 C when acclimated over a temperature range of

DRAFT

8 - 26 C. A temperature of 31.2 C was preferred by juveniles

acclimated at 24 C. A critical thermal maximum temperature

of 36.4 C was reported for juveniles, but this value was

dependent upon acclimation temperature. Significant

differences in final temperature preferenda were observed for

geographically separated populations of age-O white perch

along the mid-Atlantic coast. Adult white perch avoided

temperatures < 9.5 C and > 34.5 C.

3. White perch eggs tolerate a salinity range of 0 - 10 ppt when

exposed to a temperature range of 8 - 26 C. Larval and

juvenile perch prefer salinities of < 1.5 and < 3 ppt,

respectively. Adults exhibit a natural preference for

salinity ranging from 5 -18 ppt, while spawing occurs in

salinities < 4.2 ppt.

4. Age-O white perch survived (60%) for 19 h after exposure to

dissolved oxygen concentrations of 0.5 - 1.0 mg/L at 6.7 -

28.3 C. Adults avoided waters with < 35% saturation of

dissolved oxygen.

5. It was suggested that a short-duration (:@ 48 h) acidic pulse

to pH 6.0 could significantly reduce survival of white perch

larvae. Adult white perch presumably can tolerate a pH range

of 6.0 - 9.0.

D
w -4r
RAF i

6. Concentrations of 100 and 500 mg/L suspended solids delayed

hatching of white perch eggs 4 - 6 h. A 48 h LC50 value of

6900 mg/L was reported for larvae, while concentrations > 500

mg/L significant ly reduced survival of juveniles.

7. Toxicity data were available for various life stages of white

perch exposed to nine single chemicals. A 76 h LC50 value

of 0.27 mg/L total residual chlorine (TRC) was reported for

white perch eggs. Egg development ceased when exposed to a

concentration of 0.55 mg/L TRC. A 24 h LC50 value of 0.31

mg/L TRC was reported for larval white perch. Ninety-six h

LC50 values of 0.22 mg/L chlorine produced oxidants (CPO) and

0.15 mg/L CPO were reported for adult perch acclimated at 15

and 25 C, respectively. In addition, the length of

observation period (36 - 96 h) affected LC50 values.

8. Total chlorine was more toxic to adult white perch in

saltwater than in freshwater. A 24 h LC50 value of 2.8 mg/L

total chlorine was reported.

9. As temperature increases, the,concentration of free residual

chlorine (FRC) required to bring about an avoidance response

in adult white perch decreased. A similar relationship

existed between sal inity levels and FRC concentrations.

10. Adult white perch were more sensitive to total residual

DRAF1

oxidants (TRO) with a 2 3 C temperature increase over a

temperature range of 0 12 C. Conversely, at temperatures

of 13 - 27 C, adult perch were less sensitive to TRO with a

temperature increase and more sensitive to the TRO

concentration.

11. Ozone was more toxic to adult white perch in freshwater

than in saltwater. Ninety-six h LC50 values of 0.20 - 0.22

mg/L of ozone produced oxidants were reported for adult white

perch.

REFERENCES

Auclair, R. P. White perch in Maine. Maine Dept. Inland Fish

Game. Augusta, Maine; 1960, 16 p.

Auld, A. H. and Schubel, J. R. Effects of suspended sediments on

fish eggs and larvae. Chesapeake Bay Institute Spec. Rep.

40, Johns Hopkins Univ., Ref. 74-12; 1974, 61 p.

Block, R. M. Physiological responses of estuarine organisms to

chlorine. Ches. Sci. 18:158-160; 1977.

Block, R. M.; Rhoderick, J. C. and Gullans, S. R. Physiological

responses of white perch (Morone americana) to chlorine.

Assoc. Southeast. Biol. Bull. 24:37; 1977.

Block, R. M.; Burton, D. T.; Gullans, S. R. and Richardson, L. B.

Respiratory and osmoregulatory responses of white perch

(Morone americana),exposed to chlorine and ozone in

DRAFT

estuarine waters. In: Jolley, R. L., Gorchev, H. and

Hamilton, D. H., Jr. (eds) Water Chlorination Environmental

Impact and Health Effects, Vol. 2, p. 351-360. Ann Arbor

Science Publishers Inc., Ann Arbor, MI; 1978.

Burton, D. T. Ventilation frequency compensation responses of

three eurythermal estuarine fish exposed to moderate

temperature increases. J. Fish Biol. 15:589-600; 1979.

Burton, D. T.; Hall, L. W., Jr. and Margrey, S. L.

Multifactorial chlorine, delta temperature and exposure

duration studies of power plant effluents on estuarine

ichthyoplankton. In: Eleventh Mid-Atlantic Industrial

Wastes Conference Proceedings, p 223-229. Pennsylvania State

University Press, PA; 1979.

Dorfman, D. and Westman, J. Responses of some anadromous fishes

to varied oxygen concentrations and increased temperatures.

Water Res. Inst., OWRR Res. Proj. B-012-NJ Final Rep.,

Rutgers Univ.; 1970, 75 p.

Ecological Analysts, Inc. Hudson River thermal effects studies

for representative species: Second Progress Report.

Prepared for Control Hudson Gas and Elect. Corp.; 1978.

Gift, J. J. and Westman, J. R. Responses of some estuarine fish

to increasing thermal gradients. Ichthyological Assoc.,

Inc.; 1971, 154 p.

Gullans, S. R.; Block, R. M.; Rhoderick, J. C.; Burton, D. T. and

Liden, L. H. Effects of continuous chlorination on white

perch (Morone americana) and Atlantic menhaden (Brevootia

DRAFT

tyrannus.) at two temperatures. Assoc. Southeast. Biol..

Bull. 24:55; 1977.

Hall, L. W., Jr.; Burton, D. T. and Margrey, S. L. The effects

of chlorine, elevated temperature and exposure duration of

power plant effluents on larval white perch, Morone

americana (Gmelin). Water Res. Bull. 15:1365-1373; 1979.

Hall, L. W., Jr.; Burton, D. T. and Margrey, S. L. Acclimation

temperature: An important factor in power plant

chlorination studies with larval white perch, Morone

americana. J. Toxicol. Environ. Health 7:941-950; 1981.

Hall, L. W., Jr.; Burton, D. T.; Margrey, S. L. and Graves, W. C.

Predicted mortality of Chesapeake Bay organisms exposed to

simulated power plant chlorination conditions at various

acclimation temperatures. In: Jolley, W. A.; Brungs, J.

A.; Cotruvo, J. A.; Cummings, R. B.; Mattice, J. S. and

Jacobs, V. A. (eds) Water Chlorination Environmental Impact

and Health Effects, Vol. 4, Book 2, Environment, Health, and

Risk, p. 1005-1017. Ann Arbor Sci. Publ. Inc., Ann Arbor,

MI; 1983.

Hall, L. W., Jr.; Hocutt, C. H. and Stauffer, J. R., Jr.

Implication of geographic location on temperature

preferences of white perch, Morone americana. J. Fish. Res.

Board Can. 35:1464-1468; 1978.

Hall, L. W., Jr.; Hocutt, C. H. and Stauffer, J. R., Jr.

Temperature preference of the white perch, Morone americana,

OKAt I

collected in the Wicomico River, Maryland. Estuar. 2:129-

132; 1979.

Hardy, J. D., Jr. Development of fishes of the Mid-Atlantic

Bight: an atlas of egg, larval and juvenile stages. Vol.

III, Aphredoderide through Rachycentridae. U.S.-Fish Wildl.

Serv., Div. Biol. Serv. Prog., FWS/OBS-78/12; 1978.

Hendrey, G. R. Acidification and anadromous fish of Atlantic

estuaries. Water Air Soil Pollut. 35:1-6; 1987.

Klauda, R. J. Definitions of critical environmental conditions

for selected Chesapeake Bay finfishes exposed to acidic

episodes in spawning and nursery habitats. Technical Report

for Versar, Inc., Maryland Dept. Nat. Res.; 1989, 157 p.

Klauda, R. J. and Bender, M. Contaminant effects on Chesapeake

Bay finfishes. In: Majumdar, S. K.; Hall, L. W., Jr. and

Austin, H. M. (eds) Contaminant Problems and Management of

Living Chesapeake Ba y Resources, p. 321-372. Pennsylvania

Academy of Science, Easton, PA; 1987.

Lauers Bioassay Work. In: Environmental report, Indian Point No.

3, Appendices Vol. IV, Sect. IIIA. Consolidated Edison Co.,

NY; 1973.

Marcy, B. C., Jr. Fishes of the lower Connecticut River and the

effects of the Connecticut Yankee Power Plant. In:

Merriman, D. And Thorpe, L. M. (eds) The Connecticut River

Ecological Study: The Impact of Nuclear Power Plant, p. 61-

139. Am. Fish. Soc. Monogr. No. 1; 1976.

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McErlean, A. J. and Brinkley, H@ J. Temperature tolerance and

thyroid activity of the white perch, Roccus americanus. J.

Fish Biol. 3:97-114; 1971.

McInnich, S. P. and Hocutt, C. H. Effects of turbidity on

estuarine fish response to strobe lights. J. Appl.

Ichthyol . 3:97-105; 1987.
Meldrim, J. W. and Flava, I. A., Jr. Behavioral.avoidance

responses of estuarine fishes to chlorine. Ches. Sci.

18:154-157; 1977.

Meldrim, J. W. and Gift, J. J. Temperature preference, avoidance

and shock experiments with estuarine fishes. Ichthyological

Assoc., Inc., Bull. No. 7; Middletown, DE; 1971, 75 p.

Meldrim, J. W.; Gift, J. J and Petrosky, B. R. The effects of

temperature and chemical pollutants on the behavior of

several estuarine organisms. Ichthyological Assoc., Inc.,

Bull. No. 11; Middletown, DE; 1974, 129 p.

Meldrim, J. W.; Holstrom, E. R.; Balog, G. E. and Sugan, R. A

comparative evaluation of the effects of ozonated and

chlorinated condenser discharges on white perch, Morone

americana. Ozone Sci. Eng. 3:155-168; 1981.

Morgan, R. P.; Fleming, R. F.; Rasin, V. J., Jr. and Heinle, D.

R. Sublethal effects of Baltimore Harbor water on the white

perch, Morone americana, and hogchocker, Trinectes

maculatus. Ches. Sci. 14:17-27; 1973b.

DRAFT

Morgan, R. P. and Prince, R. D. Chlorine toxicity to eggs and

larvae of five Chespeake Bay fishes. Trans. Am. Fish. Soc.

106:380-385; 1977.

Morgan, R. P. and Prince, R. D. Chlorine effects on larval

development of striped bass (Morone saxatilis), white perch

(Morone americana) and blueback herring (Alosa aestivalis).

Trans. Am. Fish. Soc. 107:636-641; 1978.

Morgan, R. P. and Rasin, V. J., Jr. Influence of temperature and

salinity on developmen t of white perch eggs. Trans. Am.

Fish. Soc. 111:396-398; 1982.

Morgan, R. P.; Rasin, V. J., Jr. and Noe, L. A. Effects of

suspended sediments on the development of eggs and larvae of

striped bass and white perch. U.S. Army Corps Eng., Final

Rep., Append. II; Philadelphia, PA; 1973a.

Morgan, R. P.; Rasin, V. J. and Noe, L. A. Sediment effects on.

eggs and larvae of striped bass and white perch. Trans. Am.

Fish. Soc. 112:220-224; 1983.

Morgan, R. P.; Vlanowicz, R. E.; Rasin, V. J., Jr.; Noe, L. A.

and Gray, G. B. Effects of shear on eggs and larvae of

striped bass, Morone saxatilis, and white perch, Morone

americana. Trans. Am. Fish. Soc. 105:149-154; 1976.

Public Service Electric and Gas Company (PSE&G). Annuual

Environmental Operating Report (Nonradiological), Salem

Nuclear Generating Station - Unit 1; 1977 Report, Vol. 3;

Newark, NJ; 1978.

DRAFT

Rehwolt, R.; Bida, G. and Nerrie, B. Acute toxicity of copper,

nickel, and zinc ions to some Hudson River fish. Bull.

Environ. Contam. Toxicol. 6:445-448; 1971.

Rehwolt, R.; Lasko, L.; Shaw, C. and Wirkowski, C. Toxicitiy

study of two oil spill reagents towards Hudson River fish

species. Bull. Environ. Contam. Toxicol. 11:159-162; 1974.

Richardson, L. B.; Burton, D. T.; Block, R. M. and Stavola, A. M.

Lethal and sublethal exposure and recovery effects of ozone-

produced oxidants on adult white perch (Morone americana

Gmelin). Water Res. 17:205-213; 1983.

Rosenkranz, A.; Richardson, L. B. and Burton, D. T. The toxicity

of ozone produced oxidants to adult whit e perch, Morone

americana (Gmeli n). Assoc. Southeast. Biol. Bull. 25:42;

1978.

Schubel, J. R. Effects of exposure to time-excess temperature

histories typically experienced at power plants on the

hatching success of fish eggs. Estuar. Coast. Mar. Sci.
2:105-1'16; 1974.

Schubel,'J..R. and Wang, J. C_ S. The effects of suspended

sediment on the hatching success of Perca flavescens (yellow

perch), Morone americang (white perch), Morone saxatilis

(striped bass), and Alosa pseudoharengus (alewife) eggs.

Chesapeake Bay Institute Spec. Rep. 30, Johns Hopkins Univ.,

Ref. 73-3; 1973, 77 p.

Schubel, J. R.; Williams, A. D. and Wise, W. M. Suspended

sediment in the Chesapeake and Delaware Canal. Spec. Rep.

DRAFT

11, Mar. Sci. Res. Center Ref. 77-7, State Univ. New York,

Stony Brook, NY; 1977, 72 p.

Setzler-Hamilton, E. M. Utilization of Chesapeake Bay by early

life history stages of fishes. In: Majumdar, S. K.; Hall,

L. W., Jr. and Austin, H. M. (eds) Contaminant Problems and

Management of Living Chesapeake Bay Resources, p. 63-93.

Penn. Acad. Sci., Easton, PA; 1987.

Speir, H. J. Status of some finfish stocks in the Chesapeake

Bay. Water Air Soil Pollut. 35:49-62; 1987.

Stanley, J. G. and Danie, D. S. species profile: life histories

and environmental requirements of coastal fishes and

invertebrates (North Atlantic)- white perch. U.S. Fish

Wildl. Serv., Div. Biol. Serv., FWS/OBS-82/11.7; 1983, 12 p-

Terpin, K. M.; Wyllie, M. C. and Holmstrom, E. R. Temperature

preference, avoidance, shock, and swim speed studies with

marine and estuarine organisms from New Jersey.

Ichthyological Assoc., Inc., Bull. 17; 1977, 86 p.

Texas Instuments, Inc. Hudson River ecological study in the area

of Indian Point. Thermal Effects Rep.; Dallas, TX; 1976.

Wohlfarth, G. W. Decline in natural fisheries - a genetic

analysis and suggestion for recovery. Can. J. Fish Aquatic.

Sci. 43:1298-1306; 1986.

Table 1. Toxic water quality parameters adversely affecting various life stages of white
perch.

Parameter Life Stage Data Reference

Temperature Eggs Acclimation temp. = 13.5 - 14.5C. Schubel, 1974
Exposed for :!@ 1h to temp.
increases of 6 - IOC resulted in
no significant effect on
hatching success.

Temperature Eggs Normal hatch occurred at 30.5C. Ecological
Analysts,
1978

Temperature Eggs Maximum experimental hatching Morgan and
(81.5%) occurred at 14C in Rasin, 1982
freshwater.

Temperature Eggs Temperature drops of 4 to 5C Auclair, 1960
were lethal, sudden drops of 2 Hardy, 1978
to 3C induced mortality, minimum
summer temperature of 7C were
lethal; extensive mortality
occured at IOC.

Temperature Larvae Maximum length at hatch Morgan and
occurred between 16C - 18C Rasin, 1982
at all salinities (0 to 10 ppt).

Temperature Yolk sac larvae 24h TL50 = 30.2 - 31.8C C
Temperature Juvenile Exhibited temperature preference Ecological =0
@=W
of 31.2C; acclimation temp = 24C. Analysts, ON"
14d TL50 = 33.8C 1978
96h TL50 = 32.4 - 34.7C

Table 1. (Continued)

Parameter Life Stage Data Reference

Temperature Juvenile Exposure to @: 8.4C increases for Meldrim and
longer than 15 min. resulted Gift, 1971
in mortalities for fish
acclimated to temperatures
between 21.1 - 26-7C.

Temperature Juvenile 36.4C was critical thermal Dorfman and
maxima. 84% survival was Westman,
reoirted at 30-6C. 1970

Temperature Juvenile 96h TL50 = 34C Texas
Instruments!
1976
un
Temperature Juveniles Acclimated at 61, 12, 18, Hall et al.,,
24, 30, and 33C. Final 1979
temperature preferences
ranged from 15.2 - 31.OC
and were dependent upon
acclimation temperature.

Temperature YOY Collection temperature: Marcy, 1976
low 5.7C
high 40C

Table 1. (Continued)

Parameter Life Stage Data Reference

Temperature YOY Temperature preference Hall et al.,
increased as acclimation 1978
temperatures increased
from 6 - 24C. Acclimation
temperatures @: 30C resulted
in preferred temperatures less
than or equal to acclimation
temperatures. Final temperature
preferenda ranged from 31.6 -
32.5C for North Carolina
populations, 2,8.9 - 30.6 for
Maryland populations, and
29.2 - 29.6C for New Jersey
populations.

Temperature Adults Fish acclimated to 10.0, McErlean and
17.5, 20.3 and 28.5C Brinkley,
resulted in LD50 = 26.2, 1971
27.7, 29.2 and 33.2C,
respectively.

Temperature Adult organisms acclimated to 5, Burton, 1979
15 and 25C and exposed to
5C delta T experienced
ventilation rates of 35.5,
64.4, and 105.1 freq/min.,
respectively. An
acclimation temperature of
30C with a 2.5 delta T resulted
in 114.0 freq/min.

Table 1. (Continued)

Parameter Life Stage Data Reference

Temperature Adult Maximum preferred temperatures Meldrim and
recorded for white perch were Gift, 1971
32C when ambient acclimation
was 23.9C in mid July and 31.1C
when ambient acclimation was
30C in mid August. Minimum
preferred temperatures were
5C when ambient acclimation
was 1.1C and 1.7C in February.
4 - 9 ppt salinity.

Temperature Adult Acclimation between 15.5 - Meldrim and
bi .26.7C. Mortality resulted Gift, 1971
after exposure to a temperature
increase 2: 29C for -t-'15 min.

Temperature Adult Avoidance temperatures Meldrim and
ranged from 6.7C for fish Gift, 1971
acclimated to 1.1C in
February to a maximum of
35C for perch acclimated
to 25C in August.

Temperature Adult Exhibited temperature preference Ecological
of 27.8C. Analysts.,
1978

Temperature Adult Fish from New Jersey exhibited Gift and
32C avoidance temperature. Westman,
Critical thermal maximum 1971
temperature was 37.6C.

Table 1. (Continued)

Parameter Life Stage Data Reference

Temperature Adult Temperature preferena of Terpin et
23, 22.8 and 21.5C were al., 1977
reported at acclimation
temperatures of 5, 8 and
10C, respectively.
(26.5 - 27.0 ppt salinity)

Temperature Adult Seasonal upper lethal McErlean and
temperatures: Fish collected in. Brinkley,
March at 2.9C and acclimated 1971
to 10C had LD50 = 26C.
Fish collected in September
at 24.5C and acclimated
00 to 28.5C had LD50 = 33C.

Temperature Adult Fish acclimated from 1 - 26C Meldrim et
experienced avoidance al., 1974
temperatures from 7 - 37C
pH = 7.0 - 8.0.

Temperature Adult Cold shock: Fish acclimated PSE&G, 1978
at 14C in most cases survived
a delta T near 12C. Fish
acclimated at 26C and exposed
to 6C experienced total
mortality.

Table 1. (Continued)

Parameter Life Stage Data Reference

Temperature Adult Upper lethal temperature: PSE&G, 1978
Median lethal temperature for
fish acclimated at 21C was
about 33C. Exposure to 36C
resulted in 100% mortality
after 48 h. Fish acclimated
at 6C experienced 50% mortality
near 22C and 100% at 32C.
(Salinity = 3 - loppt.)

Temperature Adult At rising acclimation PSE&G, 1978
temperatures, fish acclimated
to 6C were observed to avoid
12C; those acclimated to 26C
were observed-to avoid 29 and 34C.
Upon falling acclimation
temperatures, fish acclimated
to 1C were observed to avoid
7 and 9C; those acclimated to
18C were observed to avoid
temperatures between 21 and 31C.

Temperature Adult Fish from the Hudson River Texas
exhibited temperature Instruments,
preferences between 14 - 34C. 1976
Avoidance responses occurred at
temperature < 9.5C and > 34.5C.

Salinity Eggs Salinities up to 10 ppt Morgan and
were tolerated. Rasin, 1982

Table 1. (Continued)

Parameter Life Stage Data Reference

Salinity Eggs Mean egg diameter was signi- Morgan and
ficantly greater at 0 ppt Rasin, 1982
(0.86mm) than at all higher
salinities (0.80mm). I

Salinity Larvae Usually found in salinities Stanley and
from 0 to 8 ppt, but have also Danie, 1983
been found at 30 ppt.

Salinity Juveniles From 3 ppt to 8 ppt, but rarely Stanley and
to 13 ppt. Danie, 1983

Salinity Adults Normal salinities occurred Hardy, 1978
between 5 to 18 ppt; spawning
occurred at less than 4.2 ppt.

Salinity Adults Salinities of 0.0, 6.0 and Meldrim et
12.0 ppt resulted in mean active al., 1974
oxygen consumption ranges of
115 - 961, 173 - 1740 and 222
904 mg 02 /kg-h respectively.
(Temp = 5 - 27C)

Dissolved Young of the year 40% mortality when DO = 0.5 Dorfman and
Oxygen 1.0 ppm for 19h in 10 gal. Westman,
(D.O.) chambers. 1970

Adult Levels of oxygen reduced to 35%
saturation was acceptable to fish.
(pH = 7.4 7.7, temp 8 - 21C
Salinity 2.5 - 12.5 ppt.)

Table .1. (Continued)

Parameter Life Stage Data Reference

pH Adult pH 6.0 - 9.0 was tolerated in Stanley and
freshwater. Danie, 1983

Suspended Eggs Percent hatch was not affected Morgan et
sediments by 50 - 5250 mg/L but development al., 1983
was slowed at concentrations
above 1500 mg/L during 12h
exposure.

Suspended Eggs Concentrations of 1000 mg/L Auld and
sediments significantly reduced Schubel,
hatching success. (Temp 1974
13.5 to 17.OC.)

Suspended Eggs Suspensions of natural, fine Schubel and
sediments grained sediment had no effect Wang, 1973
on the hatching success.
Concentrations of 100 and
500 mg/L resulted in a 4 - 6
h delay in hatching relative
to controls.

Suspended Eggs Concentrations of 2000 - 3250 Morgan et
sediments mg/L reduced egg development al., 1973a
to 80 - 85% of controls.

Suspended Larvae 24h LD50 = 66,989 mg/L Morgan et
sediments 48h LD50 = 6,903 mg/L al., 1973a

Table 1. (Continued)

Parameter Life Stage Data Reference

Suspended Larvae Sediment concentrations of Morgan et
sediments 1626, 2438, 3022, 5380 mg/L al., 1983
resulted in 15, 16, 17, 19*
mortality respectively.
24h LC50 = 67,000 mg/L
48h LC50 = 69,000 mg/L

Suspended Juveniles Natural, fine grained sediments Auld and
sediments @@ 500 mg/Lsignificantly Schubel,
reduced survival (p:50.05). 1974
Shear Eggs 1 min LS50 = 425 dynes/cm2 Morgan et
2 min LS50 = 415 dynes/cm2 al., 1976
5 min LS50 = 175 dynes/cm2
Shear Larvae 1 min LS50 = 415 dynes/cm2
2 min LS50 = 340 dynes/cm2
4 min LS50 = 125 dynes/cm2
Turbidity Eggs adult Has little effect but may Hardy, 1978
limit food production hence
restricting populations.

Turbidity Adult Experienced 401 avoidance at McInrich and
high turbidity (102 - 138 NTU) Hocutt, 1987
to strobe lights. Exhibited
attraction to bubble curtains
in clear and high turbidity
conditions and avoidance at low
turbidity (45 NTU).

Table 2. Toxicity data for various life stages of white perch exposed to various single chemicals.,
(NA = Not Available). All studies were static unless otherwise noted (FT = flow-through).

Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Egg Total NA (FT) NA 76h LC50 = 0.27 mg/L Morgan and
Residual Prince, 1977
chlorine
(TRC)

Egg TRC Saline 15 0.055 mg/L TRC prevented Morgan and
(2.5ppt) egg development past Prince, 1978
embryo stage.

Larvae TRC NA NA 24h LC50 = 0.31 mg/L Morgan, 1977
(FT)

Larvae TRC NA NA Larval length: decreased Morgan, 1978
(FT) significantly by 2.5 -
5.5% at > 0.5 mg/L.

Larvae TRC Saline Exposure to TRC Hall et al., 1981
3.0 15 concentrations of 0.00,
2.5 23 0.15 and 0.30 mg/L and
temperature increases of
2.6 and 10C above
acclimation temperature
for 0.08, 2.0 and 4.0 h
were conducted. Conditions
were maintained for 96h.
Larvae acclimated at
230C showed greater
mortality at all treatment
levels than those tested
at 15C.

Table 2. (Continued)

Life Chemical Water Test Data Reference
Stage Type Temperature C-
(C)

Larvae TRC saline 18C Exposed to 0.oo, 0.15, Hall et al.,
(0.5-2.5ppt) and 0.30 mg/L TRC for 1983
0.08, 2, and 4h exposure
periods at delta T's of
2, 6 and 10C above
acclimation were conducted.
Temperature change did
not affect survival. TRC
was a major factor influencing
mortality.
Adult Chlorine NA (FT) 15 96h LC50 = 0.21 mg/L Gullans, 1977
Produced
oxidants (CPO) 25 96h LC50 = 0.15 mg/L

Adult Total Saline 0-27C Avoidance to TRO(A) and Meldrim and
Residual (0-7ppt) TRO, + delta T(B): Flava, 1977
Oxidant (TRO) A. 0-12C (ambient):-
0.10-0.35 mg/L
13-27C (ambient):
0.04-0.07 mg/L
B. 0-12C (ambient) +
delta T: 0.07-0.28 mg/L
13-27C (ambient) +
delta T: 0.06-0.15 mg/L
delta T: 2-3C

.Adult TRC Saline 4-28C Avoidance mean 0.21 mg/L PSE&G, 1978
(0-8ppt)

Table 2. (Continued)

Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Adult Ozone Saline 20-27C Avoidance concentrations Meldrim et al.,
(1-2.5ppt) from 0.03 to 0.20 mg/L 1981
(mean = 0.07)

Adult Ozone Fresh 6-25.8C Avoidance concentrations
(FT) from 0.04 to 0.16 mg/L
(mean = .11 mg/1)

Adult Total Saline 22.5-28C Avoidance concentrations
chlorine (0.2-2.5ppt) from 0.01 to 0.20 mg/L
(FT)

Adult Total Fresh 7.8-26.8C Avoidance concentrations
chlorine (FT) from 0.10 to 0.36 mg/L

Adult Total Saline 24C Initial "cough" response
Ln chlorine (2ppt) at 0.02 mg/L
(FT)

Adult Ozone Saline 15-28.5C Initial "cough" response
(1-2ppt) at 0.02 mg/L
(FT)

Adult Total Fresh 5-24C Initial "cough" response
chlorine (FT) from 0.03 to 0.25 mg/L

Adult Ozone Fresh 6.5-23C Initial "cough" response
(FT) concentrations were from
0.09 - 0.17 mg/L

Table 2. (Continued)

LJ-F@ Chemical
&A, Water Test Data Reference
Stage Type Temperature
(C)

Adult Chlorine Saline 15C Physiological responses Block et al.,
produced (13.6ppt) to acute CPO exposure: 1978
oxidants (CPO) Blood pH decreased 7.6
to 6.8; hematocrit
decreased 14%: plasma
osmolality increased 35%;
no effect in PNa +; pCl-
increased 47%; pMg ++
increased > 300%; pCatt
increased 199% CA-RBC
activity increased 28% gill
Na-k ATPase decreased 93%
gill protein decreased 17%

Adult Ozone produced NA 15C 96h LC50 = 0.22 mg/L Rosenkranz
oxidants (OPO) (FT) Histological changes were et al., 1978
evident on gills within
24h of exposure to
concentrations ;-> 0.01 mg/L

Adult OPO NA 15C 96h LC50 = 0.20 mg/L. Richardson et
Blood pH significantly al., 1983
reduced when concentrations
'e 0.15 mg/L. Hematocrit
significantly increased
when concentrations @t 0.10
mg/L. Minimal effects on
gill tissue at 0.01 mg/L,
moderate epithelial sloughing
with excess mucus production
at 0.05 mg/L and severe
tissue damage when
concentrations @: 0.10 mg/L.

Table 2. (Continued)

Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Adult TCL NA NA 24-48h LC50 = 2.8 mg/L Lauers, 1973
Single 2 hour dose of
NaOCl

Adult FRC Saline 4-27C Avoidance: Meldrim et al.,
(.5-7.Oppt) 0.16 mg/1 (4C and 1974
1.5 ppt salinity)
0.10 mg/l (4C and
7 ppt salinity)
0.04 mg/1 (22C and
5 ppt salinity)
2: 0.03 mg/1 (22C and
1.5 ppt salinity)
Adult CPO Fresh 14.2-16C Blood pH decreased from Block et al.,
7.5 to 7.0 after only 1977; Block,
a 30 min exposure to a 1977
concentration of 1.3 mg/L
CPO. Hematocrit and gill
carbonic anhydrase
increased (106% and 76%,
respectively) in response
to lowered blood pH levels.
@ypothesized that hemoglobin
is oxidized to methemoglobin
in the presence of chlorine
at the gill surface, which
ultimately causes death due to
increased blood C02 and
decreased blood pH.

Table 2. (Continued)
Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Adult TRC Saline mean 96h mean TL50 0.22 PSE&G, 1978
(mean 2.7ppt) 16.9C 0.08 mg/L mean pH = 7.6
TRC + pH were only
variables to significantly
affect mean survival times
(MST). TRC was inversely
related to MST while pH
was directly related.
Adult FRC Saline FRC explained 48% of PSE&G, 1978
(0.5-7.oppt) variation in avoidance
(FT) concentration. When
chlorine contained no
FRC, estimated avoidance
concentration was 0.39 mg/L,
W whereas when chlorine was
CO 100% FRC estimated avoidance
concentration was 0.10 mg/l.
Adult No. 2 fuel oil NA 19 24-96h TL50 = 41.6- 37.2 Rehwolt et al.,
mg/L. Addition of a 1974
sublethal amount of
linear alkylate sulfonate
(LAS) eispersant a 24-96h
TLm of 3.0-1.4 mg/L was
reported.
Adult No. 4 fuel oil NA 19 24-96h TL50 = 32.0-31.0 mg/L.
Addition of a sublethal
amount of LAS resulted in a
24-96h TLm of 1.4 - 1.0 mg/L

Table 2. (Continued)
Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Adult Fuel oil NA 19 24-96h TL50 = > 500 mg/L
collecting
agent (Harder)
Adult Linear akylate NA 19 24-96h TL50 = 6.1 - 4.2 mg/L
sulfonate
(dispersant)
Adult CU NA 17 48h TL50 = 8.0 mg/L Rehwolt et al.,
96h TL50 = 6.2 mg/L 1971
Adult Zn NA 17 48h TL50 = 10.2 -mg/L Rehwolt et al.1
96h TL50 = 14.3 Ing/L 1971
Adult Ni NA 17 48h TL50 = 16.2 mg/L Rehwolt et al.,
96h TL50 = 13.6 mg/L 1971
Adult Total chlorine saline 14.5 2h intermittent exposure Meldrim et al.,
(TC) (Ippt) 96h LC50 = 0.10 mg/L 1981
Adult TC Fresh 11 96h LC50 = 0.87 mg/L
Adult TC Fresh 19 96h LC50 = 0.69 mg/L
'Adult TC Fresh.. 22 96h LC50 = 0.61 mg/L
Adult TC Fresh 26 96h LC50 = 0.74 mg/L
Adult Ozone Fresh 11 96h LC50 = 0.37 *mg/L
Adult Ozone Fresh 19 96h LC50 = 0.26 mg/L
Adult Ozone Fresh 21 96h LC50 = 0.22 mg/L
Adult Ozone Fresh 27 96h LC50 = 0.29 mg/L

Table 2. (Continued)

Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Larvae TRC Saline is Exposed to TRC Burton et al.,
(1.5ppt) concentrations of 0.00, 1979; Hall
(FT) 0.15, and 0.30 mg/L et al'., 1979
TRC and'temperature
increase of 2, 6 and 10C
above acclimation
temperature for 0.08, 2.0
and 4.0 h. Conditions
were maintained for 36h.
Temperature changes :5 10C
for :!@ 4h did not affect
survival. Mortality was
a function of TRC and
exposure duration.

CO'S

Table 3. Toxicity data for adult white perch exposed to contaminated harbor water.

Life Chemical Water Test Data Reference
Stage Type Temperature
(C)

Adult Baltimore Saline 25C Examine sublethal effects Morgan et al.,
Harbor water (5ppt) of Baltimore Harbor water 1973b
through 14d and 30d
exposures. Sublethal
effects were observed
in fish exposed to harbor
water for 30d. Biochemical
effects include increased
lactate dehydrogenase
activity within blood
serum. Also, decreased
acety1cholinesterase (brain)
and catalase levels (liver)
were reported. Physiochemical
effects include increased
thrombocyte levels, and
decreased basophil and
neutrophil levels.

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