United States

EnvlronmeAtal Protection

Agency

Office of Water

Regulations and Standards

C merla and Standards DivISion

Washington DC 20460

EPA 440/5-86~04

September 1986

&EPA

..

Water

Ambient

Water Quality

Criteria

for

Nickel - 1986

a
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR

NICKEL

U.S. ENVIRONMENTAL PROTECTION AGENCY

OFFICE OF RESEARCH AND DEVELOPMENT

ENVIRONMENTAL RESEARCH LABORATORIES

DULUTH, MINNESOTA

NARRAGANSETT, RHODE ISLAND
NOTICES

This document has been reviewed by the Criteria and Standards Division,

Office of Water Regul~tions and Standards, U.S. Environmental Protection

Agency, and approved for publication.

Mention of trade names or commercial products does not constitute

endorsement or recommendation for use.

This document is available to the public through the National Technical

Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
FOREWORD

Section 304(a)(1) of the Clean Water Act of 1977 (P.L. 95-217)

requires the Administrator of the Environmental Protection Agency to

publish water quality criteria that accurately reflect the latest

scientific knowledge on the kind and extent of all identifiable effects

on health and welfare that might be expected from the presence of pollutants

in any body of water, including ground water. This document is a revision

of proposed criteria based upon consideration of comments received from

other Federal agencies, State agencies, special interest groups, and

individual scientists. Criteria contained in this document replace

any previously published EPA aquatic life criteria for the same pollutant(s).

The term "water quality criteria" is used in two sections of the

Clean Water Act, section 304(a)(1) and section 303(c)(2). The term has a

different program impact in each section. In section 304, the term

represents a non-regulatory, scientific assessment of ecological effects.

Criteria presented in this document are such scientific assessments.

If water quality criteria associated with specific stream uses are adopted

by a State as water quality standards under section 303, they become

enforceable maximum acceptable pollutant concentrations in ambient waters

within that State. Water quality criteria adopted in State water quality

standards could have the same numerical values as criteria developed

under section 304. However, in many situations States might want to

adjust water quality criteria developed under section 304 to reflect

local environmental conditions and human exposure patterns before incorporation

into water quality standards. It is not until their adoption as part of

State water quality standards that criteria become regulatory.

Guidelines to assist States in the modification of criteria presented

in this document, in the development of water quality standards, and in

other water-related programs of this Agency, have been developed by EPA.

William A. Whittington

Director -

Office of Water Regulations and Standards
ACKNOWLEDGMENTS

Loren J. Larson

Judy L. Crane

(freshwater authors)

University of Wisconsin-Superior

Superior, Wisconsin

Charles E. Stephan

(document coordinator)

Environmental Research Laboratory

Duluth, Minnesota

Clerical Support: Terry L. Highland

Shelley A. Heintz

Diane L. Spehar

LV

Jeffrey L. Hyland

Robert E. Hillman

(saltwater authors)

Battelle New England Laboratory

Duxbury, Massachusetts

David J. Hansen

(saltwater coordinator)

Environmental Research Laboratory

Narragansett, Rhode Island
CONTENTS

Foreword ....

Acknowledgments

Tables . . . ..

Introduction.

Acute Toxicity to Aquatic Animals

Chronic Toxicity to Aquatic Animals

Toxicity to Aquatic Plants

Bioaccumulation

Other Data .

Unused Data

Summary

National Criteria

Page

111

lV

vi

1

5

8

10

11

12

14

16

17

References . . . . . . . . . . . . . . . . . . . . . . . . . . . " 54

v
1.

2.

3.

4.

5.

6.

TABLES

Acute Toxicity of Nickel to Aquatic A~imals .

Chronic Toxicity of Nickel To Aquatic Animals

Ranked Genus Mean Acute Values with Species Mean Acute-Chronic

Ratios

Toxicity of Nickel to Aquatic Plants

Bioaccumulation of Nickel by Aquatic Organisms

Other Data on Effects of Nickel on Aquatic Organisms

~C!.~

20

30

33

38

40

42
Introduction*

Nickel is one of the most common of the metals occurring 1n surface

waters (Forstner 1984; Hutchinson et al. 1975: Kopp and Kroner 1967;

Martin and Knauer 1972; Mathis and Cummings 1973; McCabe et al. 1970; Portman

1972; Solbe 1973; Trollope and Evans 1976; Young 1982). Although nickel

can exist in oxidation states of -1, 0, +1, +2, +3, and +4, under usual

conditions in surface waters the divalent cation greatly predominates

and is generally considered the most toxic. Alkalinity, hardness, salinity,

pH, temperature, and such complexing agents as humic acids influence the

oxidation state, toxicity, and availability of the nickel in aquatic

ecosystems.

Natural sources of the nickel in surface waters include weathering

of rocks, inflow of particulate matter, and precipitation. Anthropogenic

sources of nickel include the burning of coal and other fossil fuels and

discharges from such industries as electroplating and smelting. Although

fly ash can contain as much as 960 ~g/g (Swaine 1980), lake restoration

projects have experimented with the use of fly ash to remove nutrients.

Mechanisms of nickel toxicity are varied and complex (Musnak 1980),

and, as with other heavy metals, significant effects occur at cell membranes

and membranous tissues, such as gills. In fish, hematological effects

such as hyperglycemia, lymphopenia, and erythrocytosis have been reported

in association with nickel intoxication (Agrawal et al. 1979; Chaudhry

1984; Chaudhry and Nath 1985; Chaudry and Nath 1985; Gill and Pant 1981).

* An understanding of the "Guidelines for Deriving Numerical National Water

Quality Criteria for the Protection of Aquatic Organisms and Their Uses"

(Stephan et al. 1985), hereafter referred to as the Guidelines, and the

response to public comment (U.S. EPA 1985a) is necessary in order to

understand the following text, tables, and calculations.

1
Because of the variety of forms ot nickel (Callahan et al. 1979;

Nriagu 1980) and lack of definitive information about their relative

toxicities, no available analytical measurement is known to be ideal for

expressing aquatic life criteria for nickel. Previous aquatic life

criteria for nickel (U.S. EPA 1980) were expressed in terms of total

recoverable nickel <U.S. EPA 1983a), but this measurement is probably too

rigorous in some situations. Acid-soluble nickel (operationally defined

as the nickel that passes through a 0.45 ~m membrane filter after the

sample is acidified to pH = 1.5 to 2.0 with nitric acid) ~s probably the

best measurement at present for the following reasons:

1. This measurement is compatible with nearly all available data

concerning toxicity of nickel to, and bioaccumulation of nickel by,

aquatic organisms. No test results were rejected just bec~use it was

likely that they would have been substantially different if they had

been reported in terms of acid-soluble nickel. For example, results

reported in terms of dissolved nickel would not have been used if the

concentration of precipitated nickel had been substantial.

2. On samples of ambient water, measurement of acid-soluble nickel will

probably measure all forms of nickel that are toxic to aquatic life or

can be readily converted to toxic forms under natural-conditions. In

addition, this measurement probably will not measure several forms, such

as nickel that is occluded in minerals, clays, and sand or is strongly

sorbed to particulate matter, that are not toxic and are not likely

to become toxic under natural conditions. Although this measurement

(and many others) will measure soluble complexed forms of nickel,

such as the EDTA complex of nickel, that probably have low toxicities

2
to aquatic life, concentrations of these forms probably are negligible

1n most ambient water.

3. Although water quality criteria apply to ambient water, the measurement

used to express criteria is likely to be used to measure nickel in aqueous

effluents. Measurement of acid-soluble nickel probably will be applicable

to effluents because it will measure precipitates, such as carbonate

and hydroxide precipitates of nickel, that might exist in an effluent

and dissolve when the effluent is diluted with receiving water. If

desired, dilution of effluent with receiving water before measurement

of acid-soluble nickel might be used to determine whether the receiving

water can decrease the concentration of acid-soluble nickel because

of sorption.

4. The acid-soluble measurement LS probably useful for most metals, thus

minimizing the number of samples and procedures that are necessary.

5. The acid-soluble measurement does not require filtration at the time

of collection, as does the dissolved measurement.

6. The only treatment required at the time of collection LS preservation

by acidification to pH = 1.5 to 2.0, similar to that required for the

totaf recoverable measurement.

7. Durations of 10 minutes to 24 hours between acidification and filtration

of most samples of ambient water probably will not affect the result

substantially.

8. The carbonate system has a much higher buffer capacity from pH = 1.5 to

2.0 than it does from pH = 4 to 9 (Weber and Stumm 1963).

9. Differences in pH within the range of 1.5 to 2.0 probably will not

affect the result substantially.

3
10. The acid-soluble measurement does not require a digestion step, as does

the total recoverable measurement.

11. After acidification and filtration of the sample to isolate the acidsoluble nickel, the analysis can be performed using either atomic

absorption spectrophotometric or reP-atomic emission spectrometric

analysis (U.S. EPA 1983a), as with the total recoverable measurement.

Thus, expressing aquatic life criteria for nickel in terms of the acidsoluble measurement has both toxicological and practical advantages. On

the other hand, because no measurement is known to be ideal for expressing

aquatic life criteria for nickel or for measuring nickel in ambient water

or aqueous effluents, measurement of both acid-soluble nickel and total

recoverable nickel Ln ambient water or effluent or both might be useful.

For example, there might be cause for concern if total recoverable nickel

is much above an applicable limit, even though acid-soluble nickel 1S

below the limit.

Unless otherwise noted, all concentrations reported herein are expected

to be essentially equivalent to acid-soluble nickel concentrations. All

concentrations are expressed as nickel, not as the chemical tested. The

criteria presented herein supersede preVLOUS national aquatic life-water

quality criteria for nickel (U.S. EPA 1976,1980) because these new

criteria were derived using improved procedures and additional information.

Whenever adequately justified, a national criterion may be replaced by a

site-specific criterion eU.S. EPA 1983b), which may include not only

site-specific criterion concentrations eU.S. EPA 1983c), but also site-specific

durations of averaging periods and site-specific frequencies of allowed

excursions eU.S. EPA 1985b). The latest comprehensive literature search

for information Eor this document was conducted in July, 1986; some more recent

information might have been included.

4
Acute Toxicity to Aquatic Anima~~

Lind et al. (Manuscript) conducted studies on the effects of both

hardness and TOC on the acute toxicity of nickel to both Daphnia pulicaria

and the fathead minnow (Table 6). With both species, hardness was the

only significantly correlated parameter. Nebeker et dl. (1985) reported

that rainbow trout were more sensitive when 12-months old than when 3-months

old. Rehwoldt et al. (1973) observed that embryos were more sensitive

than adult snails.

Many factors might affect the results of tests of the toxicity of

nickel to aquatic organ~sms (Sprague 1985), but water quality criteria

can quantitatively take into account such factors only if enough data

are available to show that the factor similarly affects the results of

tests with a variety of species. Hardness is often thought of as having

a major effect on the toxicity of nickel in fresh water, although the

observed effect is probably due to One or more of a number ot usually

interrelated ions, such as hydroxide, carbonate, calcium, and magnes~um.

Hardness (expressed as mg CaC03/L) is used here as a surrogate for the

ions that affect the results of toxicity tests on nickel. An ~nalysis

of covariance (Dixon and Brown 1979; Neter and Wasserman 1~74) was performed

using the natural logarithm of the acute value as the dependent variable,

species as the treatment or grouping variable, and the natural logarithm

of hardness as the covariate or independent variable. This analysis of

covariance model was fit to the data in Table 1 for the four species for

which acute values are available over a range of hardness such that the

highest hardness is at least three times the lowest and the highest ~s

also at least 100 mg/L higher than the lowest. The four slopes are

between 0.69 and 1.19 (see end of Table 1) and are close to the slope

5
of 1.0 that is expected on the basis that nickel, calcium, magnesium, and

carbonate all have a charge of two. An F-test showed that, under the

assumption of equality of slopes, the probability of obtaining four slopes

as dissimilar as these is P = 0.26. This was interpreted as indicating

that it is not unreasonable to assume that the slopes for these four species

are the same.

Where possible, the pooled slope of 0.8460 was used to adjust the

acute values in Table 1 to hardness = SO mg/L. Species Mean Acute Values

were calculated as geometric means of the adjusted acute values. G~nus Mean

Acute Values at hardness = 50 mg/L were then calculated as geometric

means of the available freshwater Species Mean Acute Values (Table 3).

Of the eighteen genera for which freshwater acute values are available,

the most sensitive genus, Daphnia, was 29 times more sensitive ~han the

most resistant, Fundulus .. The freshwater Final Acute Value for nickel at

hardness = 50 mg/L was calculated to be 1,578 ~g/L uSlng the procedure

described in the Guidelines and the Genus Mean Acute Values in Table 3.

Thus, the freshwater Criterion Maximum Concentration (in ~g/L) =

(0.8460[ln(hardness)]+3.3612)

e

The acute toxicity of nickel to saltwater organisms has been determined

with 18 species of invertebrates and 4 species or fish (Table 1). The

LC50s and EC50s for invertebrates range from 151.7 ~g/L for juveniles of

the mysid, Heteromysis formosa (Gentile et ale 19~2) to 1,100,000 ~g/L for

late juvenile to adult stages of the clam, Mac~ balthica (Bryant et ale

1985). Fish are not as sensitive or as resistant to nickel. The 96-hr

LC50s range from 7,958 ~g/L for larval stages of the Atlantic silverside,

Menidia menidia (Cardin 1985) to 350,000 ~g/L for adult stages of the

mummichog, Fundulus heteroclitus (Eisler and Hennekey 1977).

6
Although data are limited, relationships might exist between both

salinity and temperature and the toxicity of nickel to some saltwater specLes.

For example, the LC50 for the mummichog is 55,000 ~g/L at a salinity of

6.9 g/kg, and 175,000 ~g/L at a salinity of 21.6 g/kg (Dorfman 1977). In

a series of tests with the amphipod, Corophium vo1utator (Bryant et al.

1985), the LC50 increased with salinity at 5°C, 10°C, and 15°C. At

salinities of 5, 10, and 15 g/kg, temperature did not seem to affect the

LC50, but at salinities of 25 and 35 g/kg, the LC50 decreased as temperature

increased. Bryant et al. (1985) found similar effects of salinity and

temperature on nickel toxicity with the clam, Macoma balthica (Table 6).

Regressions of toxicity on salinity for the above data show strong correlations.

However, analysis of covariance reveals that the slopes for the individual

species are too dissimilar (p < 0.05) to justify expressLng niCKel toxicity

as a function of salinity.

Of the twenty saltwater genera for which acute values are available,

the most sensitive genus, Heteromysis, was over 2,000 times more sensLtive

than the most resistant, Mya (Table 3). Acute values are available for

more than one species Ln each of three genera, and the range of Species

Mean Acute Values within each genus is less than a factor of 4.8. Genus

Mean Acute Values for the four most sensitive genera, Heteromysis,

Mercenaria, Mysidopsis, and Crassostrea, were within a factor of 7.8 even

though the acute tests were conducted with juveniles of the crustaceans

and with embryos of the bivalves. The saltwater Final Acute Value was

calculated to be 149.2 ~g/L, which 1S very close to the acute value for the

most sensitive tested saltwater species.

7
Chronic Toxicity to Aquatic Animals

Data are available on the freshwater chronic toxicity of nickel to

a cladoceran, a caddisfly, and two species of fish (Table 2). Nebeker

et al. (1985) conducted two early life-stage tests beginning with rainbow

trout embryos 4 hours after fertilization and one early life-stage test

beginning with trout embryos 25 days after fertilizatlon. In the first

test, weight was significantly reduced by all tested concentrations

including the lowest of 35 ~g/L. In the second test, weight was significantly

reduced by 62 and 431 ~g/L, but not by 35, 134, and 238 ~g/L, whereas

survival was reduced only at nickel concentrations of 134 ~g/L and higher.

In the third test, weight was significantly reduced at 431 ~g/L and

higher, but the reduction in survival was significant only at 1,680 ~g/L

and higher.

Lazareva (1985) conducted a Ilfe-cycLe test over successive generations

with Daphnia ~agna and observed little change in sensitivity. Although survival.

time was the most sensitive parameter 1n one test, growth was consistently

affected at a concentration of 10 ~g/L. Lazareva predicted that 5 ~g/L

would affect the productivity of populations of Daphnia magna.

The influence of hardness on chronic toxicity of nickel was investigated

by Chapman et al. (Manuscript). In life-cycle tests with Daphnia magna,

they observed an increase in chronic value with increased hardness.

Least squares regression of In[chronic value] on 1n[hardness] produced a

slope of 2.3007 with wide confidence limits (Table 2). A similar

regression with data for the fathead mlnnow produced a slope of 0.5706,

but confidence limits could not be calculated because only two points were

available for use in the regression. ~n F-test showed that, under the

8
assumption of equality of slopes, the probability of obtaining two

slopes as dissimilar as these 1S P = 0.19. This was interpreted as

indicating that it 1S not unreasonable to assume that the two slopes are

the same. The pooled slope is 1.3418 with 95% confidence limits of

-1.3922 and 4.0760. The confidence limits on the pooled acute slope are

well within the confidence limits on the pooled chronic slope.

The mysid, Mysidopsis ~~hia, is the only saltwater species with which

an acceptable chronic test has been conducted on nickel (Table 2).

Chronic exposure to nickel reduced survival and number of young at 141

~g/L and above but not at 61 ~g/L and lower (Lussier et al. 1985). Thus

the chronic value for nickel with this species is 92.74 ~g/L and the

acute-chronic ratio is 5.478.

The three available species mean acute-chronic ratios rang~ from 5.478 to

3S.5~ and were all determined with species that are acutely sensitive to

nickel (Table 3). The Final Acute-Chronic Ratio of 17.99 was calculated

as the geometric mean of the three ratios. Division of the freshwater

Final Acute Value by the Final Acute-Chronic Ratio re~ults in a freshwater

Final Chronic Value of 87.72 ug/L at hardness = 50 mg/L. Some data

(Tables 2 and 6) concerning the chronic toxicity of nickel to rainbow

trout indicate that embryos and larvae of this species might be affected

at this concentration, whereas other data (Table 2) indicate that embryos

and larvae of the species might not be adversely affected. Use of an

acute-chronic ratio that is independent of hardness is equivalent to

assuming that the chronic slop~ is equal to the acute slope. Thus the

freshwater Final Chronic Value (in ~g/L) = (O.8460(ln(hardness)]+1.64S)

e

This value might not protect ~hnia magna in soft water.

9
Division of the saltwater Final Acute Value by 17.99 results in a

saltwater Final Chronic Value of 8.293 ~g/L, which is about a factor of eleven

lower than the only chronic value that has been determined with a saltwater

species. Three of the four acutely most sensitive saltwater species are

in the same family as the specles with which the saltwater acute-chronic

ratio was determined. In addition, two other sensitive spec~es are bivalve

molluscs for which the acute values were obtained from tests on embryos

and larvae.

Toxicity to Aquatic Plants

Data on the toxicity of nickel to aquatic plants are found in Table 4.

Nickel concentrations resulting in a 40-60% reduction in growth of freshwater algae range from 50 ~g/L for the green alga, ?cenedesmus acuminatz,

to 5,000 ~g/L for the green algae, Ankistrodesmus falcatus and Chlorococcum

sp. Wang and Wood (1984) indicate that toxicity of nickel to plants is

pH dependent. Although lack of hardness values makes comparisons difficult,

general comparison of data in Table 4 with chronic toxicity data in Table 2

suggests that nickel concentrations high enough to produce chronic effects

on freshwater animals will also have deteriorative effects on freshwaLer

algal populations.

Patrick et al. (1975) found that nickel decreased diatom diversity

and caused a shift to green and blue-green algae. In their field study,

Spencer and Greene (1981) also found an increase in blue-green algae.

Using EDTA to manipulate Ni+2 concentrations, Spencer and Nichols

(1983) reported algal growth to be inversely related to free divalent

nickel and independent of total nickel concentrations.

10
Brown and Rattigan (1979) studi~d nickel tOKicity to two freshwater

vascular plants, duckweed and ~lodea (Anacharis). Despite the presence

of a thick cuticle, which protects it from many pollutants (e.g., herbicides),

duckweed was much more susceptible to nickel than was Elodea. A similar

EC50 was reported for duckweed by Wang (1986). Muramoto and Oki (1984)

observed that the water hyacinth is quite resistant, with about a 30%

reduction in growth at 4,000 and 8,000 ~g/L.

Data on the toxiclty of nickel to saltwater plants and algae are

found in Tables 4 and 6. The test with the giant kelp, Macr~stis

pyrifera, lasted four days and resulted In a 50% reduction In photosynthesis

at 2,000 )g/L (Clendenning and North 1959). The lowest concentrations

affecting growth of phytoplankton ranged from 17 to 1,800 )g/L and were

»alinity and temperature dependent (Wilson and Freeberg 1980). - Concentrations

that affect most saltwater plants apparently are higher than those that are

chronically toxic to saltwater animals.

Bioaccumulation

Data are available on bioaccumulation of nickel by a freshwater alga,

a cladoceran, and two species of fish (Table 5). The lowest factor, 0.8,

was obtained for muscle of rainbow trout. All other studies where conducted

on whole body samples and the factors ranged from 9.3 for the alga to 193

for the cladoceran. In studies with the fathead minnow, Lind et al.

(Manuscript) found that the BCF decreased as the concentration of nickel

in water increased. This same trend was observed by Hall (1982), who

studied the accumulation of nickel in various tissues of ~aphni~ magn~

and used a model to describe uptake at different exposure concentrations.

11
Watras et al. (1985) reported a BCF with ~aphni~ ~a~na or 11.6. Their study

indicated that uptake of nickel directly from the water was much greater

than uptake from food. They also suggested that little biomagnif1cation

occurs within the association of the cladoceran and algae. Jennett et

al. (1982) examined physical and biological variables affecting uptake by

algae. Although their study did not demonstrate that steady-state was

attained, Taylor and Crowder (1983,1984) studied differential uptake of

nickel by various portions of an emergent aquatic plant, the cattail.

A field study with measured nickel concentrations in a stream produced

average BCF of 803 for wild rainbow trout (Salmo gairdner~) (Dallinger

and Kautzky 1985).

Data on bioaccumulation of nickel by saltwater organtsms are available

for two species of algae and two species of bivalves (Table 5).- BCFs for

algae collected from the field are 675 for the ro~kweed, !UCUS ~~~~~losis,

and 458.3 for Ascophyl~um nodosum (Foster 1976). BCFs for bivalves

exposed for 9 days in the laboratory were 472.7 and 328.6 for the blue mussel

and 458.1 and 261.8 for the Eastern oyster (Zaroogian and Johnson 1984).

No U.S. FDA action level or other maximum acceptable concentratlon in

tissue is available for nickel, and, therefore, no Final Residue Value

can be calculated.

Other Data

Data in Table 6 suggest a high toxicity to nickel in the single-celled

organisms. Bringmann and Kuhn (l959a,b;1977a;1979;1980a,b;1981)

reported that concentrations of 2.5 to 1,500 ~g/L resulted 1n incipient

inhibition of algae, bacteria, and protozoans. Babich and Stotzky (1983)

observed delayed effects after a 24-hr exposure.

12
Willford (1966) report~d 48-hr LC50s for SlX flshes tested in the

same water. Although the fish differed in Slze. neither this nor taxonomic

differences produced a cl~ar trend in relative toxicity. BlaylocK and

Frank (1979) observed LC50s for ~arp larva at 3 and 10.5 days to be 8,460

and 750 ~g/L, respectively. Birge and coworkers obtained 28-day EC50s of

50, 60, and 90 ~g/L with embyros and larvae of rainbow trout and a 7-

day Ec50 of 50 ~g/L with embryos and larvae of the narrow-mouthed toad.

Shaw and Brown (1971) studied the effect of nickel on laboratory

fertilization of rainbow trout eggs. They did not find a statistically

significant effect at 1000 ~g/L (hardness = 260 to 280 mg/L) and noted a

stimulation in development after fertilization compared to controls.

Whitley and Sikora (1970) and Brkovic-Popovic and Popovic (1977b)

studied ~ffects on respiration in tubificid worms. Influence of nickel

on thermal resistance of salmonids was examined by Becker and Wolford

(1980). The effect of complexing a~ents on toxicity of nickel to carp

was studied by Muramoto (1983). Smith-Sonneborn et al. (1983) studied

the toxicity of nickel dust particles ingested by Parameciu~. Anderson

(1973) and Anderson and Weber (1~75) derived an expression r~latlng body

size to sensitivity of the guppy.

In a field study, Havas and Hutchinson (1982) worked with acidified

and control ponds and suggested that the lowered pH increased the concentrations of heavy metals such as nickel and stressed resident aquatic

invertebrates. Keller and Pitblado \19~4) and Yan et al. (1985) compared

ambient nickel concentrations to aquatic community dynamics.

Available data that were not used directly in the derivation of

saltwater criterion for nickel (Table 6) do not indicate a need to lower

the criterion. In addition to affecting survival of saltwater animals,

13
nickel affects growth, development, reproduction, and bloch~mical responses.

A 19% reduction in growth of juvenile Paciflc oysters, ~ra~s~_~rea ~~~a~,

exposed to 10 ~g/L for 14 days at a salinity of 34 g/kg was reported by

Watling (1983). The ecological significance of this reduction is unknown,

but after 14 days tn clean water size was similar to that of the controls.

Petrich and Reish (1979) found that 100 to 500 ug/L suppressed reproduction

of a polychaete, Ctenodri!~ ser~~~. Zaroogian et a1. (982) showed a

significant reduction in ATP activity in the adductor muscle of the blue

mussel, but not the Eastern oyster, after a la-week exposure to 10 ~g/L.

Abnormal development of embryos of the sea urchins, Arbac ia pun<;_tu~a.t:..~. and

Lvtechinus pictus, occurred at several concentrations of nickel (Timou.rian

and Watchmaker 1972; Waterman 1937), and concentrations as low as 58.69

~g/L depressed sperm motility in gametes of the purple urchin, Strongy"locentrotus

purpuratus (Timourian and Watchmaker 1977).

Unused Data

Some data on the effects of nickel on aquatic organlsms were not used

because the studies were conducted with species that are not resident in North

Amenca (e.g., Ahsanullah 1982; Ballestoi!r and Castellvi 1979: Baudouin

and Scoop a 1974; Kanai and Wakabayashi 1984; Khangarot et al. 1982: McFeters

et a1. 1983; Saxena and Parashari 1983; Srivastava et al. 1985: Van H"of and

Nauwelaers 1984; Verma et al. 1981; Wilson 1983). Results (e.g., Kissa

et a1. 1984) of tests conducted with brine shrimp, ~r~5;~i~ ~..e..., were not

used because these specles are from a unique saltwater environment.

Data were also not used if nickel was a component of a mixture (e.g.,

Alman and Bager 1984; Anderson 1983; Besser 1985; Cowgill et ai. 19~6,

Doudoroff 1956; Doudoroff et al. 1966: Eisler 1977b; Hutchlnson and

14
Sprague 1983,1986; Lopez-Avi la et al. 1985; Markarian et a1. 1980: Muska

1978; Muska and Weber 1977a,b; Phelps et al. 1981; Su10way et a1. 1983;

Stratton and Corke 1979b; Vymazal 1984; Weinstein and Anderson 1978; Wong

and Beaver 1980; Wong et al. 1978,1982), an effluent (e.g., Abbe 1982;

Blaise and Couture 1984; Cherry et al. 1979; Jay and Muncy 1979; Lewis

1986) or sediments (e.g., Malueg et al. 1984; Seeleye et al. 1982).

Babich and Stotzky (1985), Bidding~r and Gloss (1984), Birge and

Black (1980), Chapman et al. (1968), Doudoroff and Katz (1953), Eisler

(1981), Jenkins (1980), Kaiser (1980), LeBlanc (1984), McKim (1977),

Phillips and Russo (1978), Rai et al. (1981), Thompson et al. (1972),

and U.S. EPA (1975) only contain data that have been published elsewhere.

Christensen et al. (1985) reported computer simulated data only.

Data were not used if the organisms were exposed to nickel tn food (e.g.,

Cowgill et al. 1985; Mansouri-Aliabadi and Sharp 1985; Windom et al.

1982). Results were not used if the test procedures were not adequately

described (e.g., Bean and Harris 1977; Braginskiy and Shcherban 1978;

Brown 1968; Jones 1939; Petukhov and Ninonenko 1982; See et al. 1974,1975;

Shcherban 1977; Sirover and Loeb 1976; Soeder and Engelmann 19~4; Wdng et

al. 1984). The 96-hr values reported by Buikema et al. (1974a,b) were

subject to error because of possible reproductive interactions (Buikema

et al. 1977). Michnowicz and Weaks (1984) conducted tests at too Iowa

pH. Babich et a1. (1986) only exposed cell cultures.

Results of some laboratory tests were not used because the tests were

conducted in distilled or deionized water without addition of appropriate

salts (e.g., Jones 1935; ~acDonald et a1. 1980; Shaw and Grushkin 1957)

or were conducted in chlorinated or "tap" water (e.g., Grande and Andersen

1983; Janauer 1985). Dilution waters in studies by Mann and Fyfe (1984)

15
and Stratton and Corke (1979a) contain~d exceSSlve amounts of EDTA. Stokes

(1975) and Whitton and Shehata (1982) used algae from waters conta1ning

high concentrations of nickel. The data of Gerhards and Weller (1977) on

accumulation of nickel by algae were not used because the test concentrations

of nickel adversely affected the growth of the algae. Dugan (1975)

reported results in uptake studies only as counts of radio-labeled nickel.

Bringmann and Kuhn (1982) cultured Daphnia magna in one water and

conducted tests in another. Tests conducted with too few test organisms

(e.g., Applegate et a1. 1957; Tarzwell and Henderson 1960) were not used.

Reports of the concentrations of nlckel in wild aquatic organlsms

(e.g., Abo-Rady 1979; Amemiya and Nakayama 1984; Bailey and 5tokes 1985;

Bosserman 1985; Bradley and Morris 1986; Brezina and Arnold 1977; Bryan

et al. 1983; Chapman 1985; Chassard-Bouchard and Balvay 1978; Dunstan et

al. 1980; Eisler et al. 1~78; Gordon ~t a1. 1980; Guilizzoni 1980; Hall

et al. 1978; Heit and Klasek 1985; Jenkins 1980; Kawamata et al. 1983;

La Touche and Mix 1982; McDermott et al. 1976; McHardy and George 1985;

Martin 1979; Mathis and Cummings 1973: Mears and Eisler 1977; O'Conner

1976; Ozimek 1985; Parsons et a1. 1972; P~nnington et al. 1982; Pulieh

1980; Reynolds 1979: Stokes et al. 1985: Tong eL al. 1974; Trollope and

Evans 1976; Uthe and Bligh 1971; Van Coille and Rousseau 1974; Wachs 1982;

Wehr and Whitton 1983; Wren et al. 1983) were not used to calculate

bioaccumulation factors due to the absence or insuffici~nt numb~r ot

measurements of nickel in water.

Summary

Acute values with twenty-one freshwater specles 1n 18 genera range

from 1,101 ~g/L for a cladoceran to 43,240 ~g/L for a fish. Fishes and

16
invertebrates are both spread throughout the range of sensltivity. Acute

values with four species are significantly correlated with hardness.

Data are available concerning the chronic toxicity of nickel to two

invertebrates and two fishes in fresh water. Data available for two

species indicate that chronic toxicity decreases as hardness lncreases.

The measured chronic values ranged from 14.77 ~g/L with Daphnia magna

in soft water to 526.7 ~g/L with the fathead minnow in hard water. Five

acute-chronic ratios are available for two species in soft and hard water

and range from 14 to 122.

Nickel appears to be quite toxic to freshwater algae, wlth concentrations

as low as 50 ~g/L produclng significant inhibition. Bioconcentration

factors for nickel range from 0.8 for fish muscle to 193 for a cladoceran.

Acute values for twenty-three saltwater species in twenty genera range from

151.7 ~g/L with juveniles of a mysid to 1,100,000 ~gjL with juveniles and adults

of a clam. The acute values for the four species of fish range from 7,598 to

350,000 ~g/L. The acute toxicity of nickel appears to be related to salinity,

but the form of the relationship appears to be species-dependent.

Mysidopsis bahia is the only saltwater species with which an acceptable

chronic test has been conducted on nickel. Chronic exposure to 141,~g/L

and greater resulted in reduced survival and reproduction. The measured

acute-chronic ratio was 5.478.

Bioconcentration factors In salt water range from 261.8 with a oyster

to 675 with a brown alga.

National Criteria

The procedures described in the "Guidelines for Deriving Numerical

National Water Quality Criteria for the Protection of Aquatic Organisms

17
and Their Uses" indicate that, except possibly where a lucally important

species is very sensitive, rreshwater aquatic urganisms and their uses

should not be affected unacceptably if the four-day average concentration

(in ~g/L) of nickel does not exceed the numerical value given by

(0.8460[ln(hardness)]+l.l64S) more than once every three years on the

e

average and if the one-hour average concentration (in ~g/L) does not

exceed the numerical value given by e (0.8460[ln(hardness)]+3.3612) more

than once every three years on the average. For example, at hardnesses

or so, 100, and 200 mg/L as CaC03 the rour-day average concentrations of

nickel are 88, 160, and 280 ~g/L, respectively, and the one-hour average

concentrations are 790, 1400, and 2500 ~g/L.

The procedures described in the "Guidelines for Deriving Numerical

National Water Quality Criteria for the Protection of Aquatic ~rganisms

and Their Uses" indicate that, except possibly where a locally important

speC1es 1S very sensitive, saltwater aquatic organisms and their uses

should not be affected unacceptably if the rour-day average concentrat1on

of nickel does not exceed 8.3 ~g/L more than once every three years on the

average and if the one-hour average concentration does not exceed 75 ~g/L

more than once every three years on the average.

"Acid-soluble" is probably the best measurement at present for expressing

criteria for metals and the criteria for nickel were developed on this

basis. However, at this time, no EPA approved method for such a measurement

is available to implement criteria for metals through the regulatory

programs of the Agency and the States. The Agency 1S considering development

and approval of a method for a measurement such as "acid-soluble." Until

one is approved, however, EPA recommends applying criteria for metals

using the total recoverable method. This has two impacts: (1) certain

18
spec1es of some metals cannot be measured because the total r~cvverable

method cannot distinguish between individual oxidation states, and (2) 1n

some cases these criteria might be overly protective when based on the

total recoverable method.

Three years is the Agency's best scientific judgment of the average

amount of time aquatic ecosystems should be provided between excurS10ns

(U.S. EPA 1985b). The resiliencies of ecosystems and their abilities to

recover differ greatly, however, and site-specific allowed excursion

frequencies may be established if adequate justification is provided.

Use of criteria for developing wat~r quality-based permit limits and

for designing waste treatment facilities requires selection of an appropr1ate

wasteload allocation model. Dynamic models are preferred for the application

of these criteria (U.S. EPA 1985b). Limited data or other cons~derations

might make their use impractical, 1n which case one must rely on a steady-state

model (U.S. EPA 1986).

19
Table I. Acute Toxicity of Nickel to Aquatic Animals

Hardness LC50 Adjusted Species Mean

(mglL as or EC50 LC50 or EC50 Acute Value

Species Method· Chemical caCO~ (Ilg/U" (Ilg/U"· (Ilg/U..•• Reference

FI<ESHWATER SPECIES

Worm, S, M 50 14,100 14,100 14,100 Rehwol dt at dl. 1'J75

Nals SP.

Snail (embryo) , S, M 50 11,400 11,400 Rehwo Idt et al. 197;

Amnlcola sp.

Snail (adult), S, M 50 14, ~OO 14, ~OO 12,710 Rehwoldt et al. 1975

Amn Ic~ sp.

CIadoceran, S, U Nlck~1 <~17 Anderson 1948

Daphn @ magna chloride

C ladocerdn, S, U Nickel 45.3 510 554.4 BIes Inger and

paphn Ia _magna chloride Christensen 1972

Clac1oceran, S, Nickel 51.1 915 898.3 Call at al. 1983

Oaphn_@ magna nitrate

C Iadocaran, S, Nickel 51 1,800 1,710 Chapman et al •

Daphnia magna chloride Manuscript

tv

0 Cladoceran, S, M Nickel 100 2,360 1,313 Chapman et al •

Q.aphn i a maqna Chloride Manuscript

Cladoceriln, S, ,~ Nickel 104 1,920 1,033 Chapman et al •

Daphn Ia _magna Chloride Manuscr Ipt

Cladoceran, S, M Nickel 206 4,970 1,500 1,102 Chapman et al.

Daphn @ magna chlorlc1a Manuscript

CIadocaran, S, M Nickel 48 2,182 2,259 LI nd at al •

Daphnia pul~~drla sulfate Manuscript

CIildoceran, 5, M Nickel 48 \,813 1,877 LI nd et al.

DaDhn..l~ ~Llcaria sui tate Manuscript

Cladocaran, 5, M Nickel 44 11,836 2,046 Lind at al.

Daphnia pulicarla su Ifate Manuscript
Tlible 1. (Continued)

Hardness LC50 Adjusted Species MelIn

(mglL as or EC50 LC50 or EC50 Acute Value

Species Method· Chemical (lig/U" (lig/U"· (IIS/U.... Reference

Cladoceran, 5, M Nickel 47 1,901 2,003 2,042 LInd et al.

Daphnia pul Icarla sulfate Manuscript

Amphlpod, 5, M 50 13,000 n,ooo 13,000 Rahwoldt at al. 1973

Gammarus sp.

Mayfly, 5, U NI ckel 42 4,000 4,636 4,636 Warn Ick and Bell

iE.hemerella subvar la su Ifate 1969

Damsel fly, 5, M 50 2\ ,200 21,200 21,200 Rahwoldt et al. 1973

Unidentified sp.

Stonefly, 5, U Nickel 40 33,500 40,460 40,460 Warnick and Bel I

Acroneurla Iycor~ sulfate \969 ------

Caddlsfly, 5, M 50 30 ,200 30,200 30,200 Rehwoldt et al.

Unldent If i ed sp. 1973

American eol, 5, M Nickel 53 n,ooot 12,370 Rehwoldt at al.

~~rostrata nitrate \971

N Amer Ican 8e I , 5, M 55 13,000 11,990 12,180 Rehwoldt et al. r- ~~ rostrata 1972

Ral nbow trout (2 mos), F, M Nickel ~5,500 Hale \977

Salmo galrdnerl nitrate

Rainbow trout (juvenile), F, ~~ Nickel 20, lOOt Anderson 1981

2.-a1mo 2irdneri sulfdte

Rainbow trout (juvenile), F, M Nickel 12,700t Anderson 19tH

Salmo qalrdneri sulfate

Rainbow trout (juvenile), F, M Nickel 28,000t Anderson 1981

~~ qa Irdner i 5U q dte

Rainbow trout (juvenile), F, M Nickel ~0,900t Anderson 1981

Salmo galrdneri sulfate

Ra Inbow trout (juvenile), F, M Ni ckel 16,900t Anderson 19tH

Salmo galrdnerl sui fate
TlIble 1.

CcontInued)

Hardness LC50 Adjusted Species Mean

CmglL as or EC50 LC50 or EC50 Acute Value

Species Method· Chemical Cllg/U" C\lg/U·" Ceg/

U .... Reference

Rainbow trout (juvenl Ie), f,

M Nlckal 15,900

t Anderson 1981

Salma qairdnerl 5ul ti'lte

Halnbow trout (.juvenile), f,

M Nlckal 11

• ~OOt Anderson 1981

Salmo qairdneri 5ultate

Rainbow trout (juvenl Ie). f,

M "llckel 11,I00

t Anderson 1981

Salmo galrdnerl su

Itate

Rainbow trout (~ mos)

• f.

M Nickel 27- 10.000 14.210 Nebeker et al. 1985

Salmo galrdnerl chloride ~9

Rainbow trout (~ mos)

• f.M Nickel 27- 10,900 15.490 Nebeker et al. 1985

~I m~ ~!!dneri chlorl<1e ~9

Rainbow trout (12 mos)

, F.M Nickel 27- H.900 12.6')0 Nebeker et al. 1985

Salmo galrdnerl chi or Ide ~9

Rainbow trout (12 mos)

• F,

M Nickel 27- 8,100 11.510 13,380 Nebeker et al. 1985

Salmo galrdnerl chloride 39

Goldtish (1-2 q). S,

U Nickel 20 9,820 21,320 21,320 Pickerlnq and

IV Carasslus auratus chlor Ide Henderson 1966 IV

Common carp «20 em)

, S,M Nickel 5~ 10,600

t 10,090 Rehwoldt et al.

Cyprlnus carpio nitrate 1971

Common carp. S,

M 55 10,400 9,594 9,839 Rehwoldt at al.

S:VprInus carp!.£ 1972

Fathead minnow (1-2 9), S,

U Nickel 20 5,180 11,250 Pickering and

Plmephales promelas ch lor ide Henderson 196b

Fathead minnow (1-2 g)

, S, 1I Nickel 20 4.580 9,943 Picker

Ing and

~Imephales promelas chloride Henderson 1966

Fathead minnow (1-2 g), S.

U Nicke

I ~60 42,400 7,981 Pickering and

£,Imephales prome~ chloride Henderson 1960

Fathei'ld minnow (1-2 g). S,

U "llcke

I 360 44,500 8,376 Pickering and

Plmephales promelas chloride Henderson 196b
Tab leI. (continued)

Hardness LC50 Adjusted Spec les Mean

(mglL as or EC50 LC50 or EC50 Acute Val ue

Species Method· Chemical (\lg/U" (\lg/U·" (\lQ/U..•• ReferencA

Fathead minnow (Immature), S, U Nickel 210 27,000 8,019 Pickering 1974

Plmephales promelas chloride

Fathead minnow (Immature), S, M Nickel 210 32,200 9,563 Picker I ng 1974

Plmephales promelas chloride

Fathead minnow (Immature), F, M Nickel 210 28,000 8,316 Plckerlnq 1974

Plmephales promelas chloride

Fathead minnow (Immature), F, M Nickel 210 25,000 7,425 Pickering 1974

Plmephales promelas chloride

Fathead minnow, F, M Nickel 45 5,209 5,61)5 LI nd at al.

PI mepha Ies .£!"~~ sulfate Manuscript

Fathead minnow, F, M Nickel 44 5,163 5,753 8,027 LI nd at ale

Plmephales _promelas sulfate Manuscript

Banded killi fish «20 em) , 5, M Nickel 5~ 46,200 t 43,980 Rehwoldt et al •

fundulus dlaphanus nitrate 1971

N Banded kill Ifish, S, M 55 46,100 42,530 43,250 Rehwoldt et al.

w fund~~ dlaphanus 1972

Guppy (6 mol , 5, lJ Nickel 20 4,450 9,661 9,661 Plckerlnq and

Poecilia retlculata chloride Henderson 196fl

White perch «20 em) , S, M Nickel 53 13,600 t 12,950 Rehwo Idt at al.

~~ americana nitrate 1971

Wh Ite perch, 5, M 55 13,700 12,640 12,790 Rehwo Id1 ut al.

Morone americana 11)72

Str Iped b<lsS (flnqerl Inq), S, M Nickel 53 6,200t 5,902 Rehwoldt at al.

Morone saxatilis nitrate 1971

Striped bass, 5, M 55 6,300 5,B12 Rehwo Id t et al.

Morone saxati I is 1972 ----

Striped bass (63 day) , 5, lJ Nickel 40 3,900 4,710 Palawskl et al. 1985

Morone si1xat I I Is chlor ide --------
Table 1. (continued)

Hardness lC50 Adjusted Spec I es Mean

(mg/l as or EC50 LC50 or EC50 Acute Value

Species Method· Chemical (lIg/U" (1I9/U"· (!!g/U·..• Reterence

Str I pad bass (63 day) , 5, U Nickel 285 33,000 7,569 5,914 Palawskl et al. 19t:b

Marone saxatl I 15 chloride ------

Rock bass, F, M f-lickel 26 2,480 4,312 4,312 Lind at al.

Amblop lites rupestr 15 su I fate Manuscr Ipt

Pumpk I n seed «20 cm), 5, M Nickel 53 8, lOot 7,710 Rehwoldt at al •

Lepomls qlb~ nitrate 1971

Pumpk I nseed, 5, M 55 8,000 7,380 7,544 Rahwoldt et al.

Lepomls _9.~osus 1972

BI USC] I II (1-2 q), 5, U Nickel 20 5,180 11,250 Plckarlnq and

Lepom 15 _macroch I rus chlor Ide Henderson 1966

A I ueqlll (1-2 q), 5, U Nickel 20 5,360 11,640 Pickering and

Lepomls macrochirus chloride Henderson 1966

Ii I usq I I I (1 - 2 q), 5, U Nickel 360 39,600 7,454 Plckerlnq and

Lepomls macrochirus chloride Henderson 1966

N

.j:'- B lueg III, F, M Nickel 49 21,200 21,570 12,040 Cairns et al. 19tH

Lapomls macrochlrus chloride
Tab Ie 1. (continued)

LC50 Species Melin

Salinity or EC50 Acute Value

Species Method- Chemical (g/kg) (pg/U" (lJglU Reference

SALTWArER SPEC IES

Polychaete OIorm (adult), S, U tn ckel 49,000 49,000 Petr Ich and Reish 1979 I~erols arenaceodentata chloride

Polychaete OIorm (adult), S, U I~ickel 20 L5,OOQ 25,000 Eisler and Hennekey 1977

Nereis vlrens' chloride

Polychaete worm (adult), S, U Nickel 17,000 17,000 Petrich and Rei sh 1979

Ctenodrl Ius serratus ch lor Ide

Polychaete OIorm (adult), S, U Ni cktd >50,000 >50,000 Petr ich and Rei sh 1979

Capltelld capitata ch lor Ide

Mud soa; I (adult), S, U NIcke I 20 72 ,000 72,000 Eisler and Hennekey 1977

Nassar Ius obsoletus ch lor Ide

Eastern oyster (embryo), S, U I~I ckel 75 1,180 1,180 Cal abrese at al. IlJ/3 Crd~sostrea virglnlca chloride

Clam, S, U Nickel 15 100,000 l3rydnt et al. 1<)85

Nacoma balthicd chloride (5°C)

N Clalll, S, U Nickel 25 380,000 13ryant 8t al • 1985 V1

Macontd bdlthlca chloride (5°C)

Clam, S, U Nickel 35 700,000 Bryant et al. 1985

Macoma balthica chloride (5°C)

Cldm, S, U Nickel 15 9':>,000 Bryant et 01. 1985

Mdcoma balthica ch lor Idu <lO°C)

Clam, S, U Nickel 25 560,000 Bryant et al. 19t15

Macomd balthicd chloride (10°C)

Clam, S, U Nickel 35 1,100,000 Bryant et al. 1<)t.l5

Macoma balthica ch lor id", (J 0 °C)

CldlO, S, U Ni ckl;\ 15 110,000 Bryant at al. 1985

Macoma balthlca chlo,.IJe (J 5 °C)
Table 1. (continued)

LC50 Species Mean

Salinity or EC50 Acute Value

Species Method* Chemical

( g1kg) (pg/U

n (lJg/U Reference

CIdln, S,

U Nlckd 25 WO,OOO Bryant et al• 19ti5

r~acomd billthlca chloride

( 1'J°C)

Clam, S,

U NIckel 35 540,000 294,500 Uryant et al. 1985

Macoma bdlthlca chloride

( 15°C)

Quahog clam (&nbryo), S,

U Nickel 25 310 310 Calabrese and Nelson

Mercendrla mercenarla chloride 1974

Soft-shell clam (adult), S,

U Nickel 20 320,000 Eisler and Hennekey 1977

Mya arenarla chloride

Soft-shell cldm (adult)

, S,

U Nickd 30 >50,000 320,000 Eisler 1977a

Mya arendrla chloride

Copepod (adult), S,

U Nickel 30 13,180 Lussier and Card In 1985

Eurytemora affln

i

s chloride

Copepod (adult), 5,

U Nlck",1 30 '),593 11,240 Lussier and Cardin 1985

Eurytemora affinis chloride

Copepod (adult), S,

U NiCkel 30 3,466 3,466 Lussier and Cardin I'Jd5

Acartid c1au~I chloride

N

0\ Copepod (adu It)

, S,U NIcked

7 b,OOO 6,000 oongtsson 1978

Nltocrd splnlpes chloride

Mysld <juIJenile), 5,

M Nickel 30 151 .7 151.7 Gentile et al. 19132

lIeteromysls formosa chloride

Mysld (juIJenlle), F, r~ Nlckul 30 508 508 Gentile et al. 1')82;

Mysldopsis bdhia chloride Lussier et al. 1985

~lys Id (j uIJen lie), 5, ~~ tlickel 30 634 634 Gentile et al. 1982

Mysldopsls bigelowl chloride

Amphlpod, 5,

U Nickel

5 5,000 Bryant et al. 1985

Corophlum IJolutator ch lor

Ide (5°C)

Amphipod, 5,

U NIC'kel 10 21,000 Bryant et al. 1985

Corophlum IJolutator ch lor ide (5°C)
Table 1. (continued)

LC50 Species Mean

Salinity or EC50 Acute Value

Species Method* Chemical (g/kg) (pg/U** (lJg/U Reference

Amphipod. S.U Nickel 15 18.000 Bryant at al. 1985

Coroph tum volutator Chloride (5°C)

Amphlpod. S.

U

NIckeI 25 36,000 l3ryant at al. 1985

Coraph tum volutator ch lor

I<je (5°C)

Amphlpod. S.

U Nickel 35 54.000 Bryant at al. 1985

Corophlum volutator chloride (5°C)

Amphlpod. S.

U Nickel

5 3.000 Bryant et al. 1985

Corophlum volutator chloride <10 °C)

Amphlpod.S

U Nickel 10 15.000 Bryant at al. 1985

• Corophium volutator chloride <10 "C)

Amphlpod. S.

U Nickel 15 22.000 Bryant at al. 1985

Corophium volutator chloride <10 °C)

AlnphIpod. S.

U

NIekel 2? 24.000 Bryant at al. 1985

Curophlum volutator chloride <1 O°C)

Amphipod. S.

U Nickel 35 52.000 Bryant at al. 1985

Corophlum volutator ch lor ide

(10

0 e)

N

---.J Amphlpod. S.

U Nickel

5 5.600 Bryant at al. 1985

Corophlum volutator chloride (15 "C)

Amphlpod. S.

U Nickel 10 16.000 Bryant ot al. 1985

Corophlum volutator chloride <15°C)

Amphlpod. S.

U Nickel 15 IS.000 Bryant at al. 1985

CorophIurn volutator Chloride <15 °C)

Amphlpod.

S

.

U NiCkel 25 22.000 Bryant at al. 1985

Corophlum volutator chloride <15 °C)

Amphlpod. S.

U Nickel 35 34.000 18.950 Bryant et al. 1985

CorophIU1n volutdtor chloride (15°C)

Hermit crab (adult). S.U Nickel 20 47.000 47.000 Eisler and Hennekey 1977

Pagurus longlcarpus chloride
Table 1. (continued)

Species Method· Chemical

Starfish (adult), S, U Nickel

Asterlas forbesll chlor Ide

Mumm Ichog (adult), S, U Nickel

Fundulus heteroclltus chlor Ide

Mummlchog (adult) , S, U NIckel

Fundulus heteroclltus ch lor Ide

Mumm Ichoq (adult) , 5, U Nickel

Fundulus heteroclltus chlor Ide

Atlantic sllllerside S, U Nickel

(Iarlla), chlor Ide

Menldla menldla

TIdewater slillers Ide S, U NIckel

(j ullen II e) , chi or Ide

Menldla penlnsulae

N Str Iped bass (63 day) , 5, U Nickel 00 Morone saxatll Is chlor Ide

Spot (jullenlle), 5, U Nickel

Lelostomus xanthurus chlor Ide

Salin Ity

(g/kg)

20

6.9

21.6

20

30

20

21

lC50 Spec I es Mean

or EC50 Acute Value

(liglL)•• ("gIL) Reference

150,000 150,000 Eisler and Hennekey 1977

55,000 Dorfman 1971

175,000 Dortman 1971

350,000 149,900 E I sl er and Hennekey 1977

7,958 7,958 Card In 1985

38,000 38,000 Hansen 1983

21,000 21,000 Palawskl et al. 1985

70,000 70,000 Hansen 1983

1I1i

s = statIc; R = renewal; F = flow-throuqh; M = measured; U

Results are expressed as nickel, not as the chemical.

unmeasured •

llllllll

t

Freshwater LC50s and EC50s were adjusted to hardness = 50 mg/L (as CaC03) using the pooled slope of 0.8460 (see text).

Freshwater Spec les M3an Acute Val ues are cal cui ated at hardness = 50 mg/L (as CaCD3 ).

In r Iller water.
N

\.0

Table 1. (continued)

Results of Covariance Analysis of Freshwater Acute Toxicity versus Hardness

Species n Slope 95_ Confidence Limits Degrees of Freedom

Daphn la magna 6 1.1810 0.3187, 2.0433 4

Fathead ml nnow 10 0.8294 0.6755, 0.9833 8

Striped bass 4 1.0459 0.7874, 1.3045 2

Bluegill 4 0.6909 -0.1654, 1.5472 2

All of above 24 0.8460* 0.7004, 0.9915 19

It P 0.26 for equality of slopes with 16 degrees of freedan.
Table 2. Chronic Toxicity of Nickel to Aquatic Ani....

Hardness

CIIg/L .. U.lts ChrOille Vel..

Species J.!!!.I' Ch.'cal C~) C,s/U" hg/L) Reference

FRESHWATER SPECIES

CI~doceran, LC Nickel 51 10.2- 14.77 Chapman et al.

Daphn la magna chloride 21.4 Manuscr Ipt

Cladoceran, LC Nickel 105 101- 123.1 Chapmi!ll at al •

Daphn la magna chloride 150 Manuscript

CI adoceran, LC Nickel 205 220- }56.6 Chapmi!ll at al.

Daphn la magna chloride 578 "'anuscr Ipt

CI ~doceran (1st generation) , LC Nickel 5-10 7.071 Lazareva 1985

Daphnia magna sui fate

CI adoceran (2nd generation) , LC Nickel <5**- <5 Lazareva 1965

Daphnia magna sulfate

Cladoceran Ord generation) • LC Nickel 5-10 7.071 lazareva 1965

Daphn la magna ~ulfate

CI adoceran (4th generation) , lC Nickel 5-10 7.071 lazareva 1965

w Daphn I a magna sulfate

0

Caddlstl", LC Nickel 54 66- 126.4 Nebeker at al. 1984

C II storon la magnifica chloride 250

Ra Inbow trout, ElS Nickel 5} <35"- <35 Nebeker et ~I • 1985

galrdnerl chlor Ide

Ra Inbow trout, ElS Nickel 52 62- 91.15 Nebeker et al. 1985

galrdnerl chlor Ide 134

Ra Inbow trout, ELS Nickel 49 134- 240.3 Nebeker et al • 1985

galrdnerl chlor Ide 431

Fathead minnow, LC Nickel 210 360- 526.7 Picker Ing 1974

Plmephales promelas chlor Ide 730

Fathead minnow, ElS Nickel 44- 108.9- 217.3 Lind etal.

Plmephales promelas sui fate 45t 433.5 Manuscript

----~------~---
Tabl. 2. (CoAtlnued)

Specl.S Salinity

(g/kg)

U.lts

(pgA)•• a.ronic Val..

"gIll R.ference

Mysld,

Mysldopsls bahla

LC Nickel

chloride

SALTWATER SPECIES

30 61-

141

92.14 Gentile et al. 1982;

Lussier et al. 1985

• LC :: lite-cycle or plIrtlal lite-cycle; ELS :: earl y lite-stage•

•• Results are based on measured concentrations of nickel.

AAA Unacceptable effects occurred at all concentrations tested.

t \lal ues from a:;ute tests In Table 1.

o

2

Spec••s n Slope 95' Conf.dence l,.,ts

oaphn I a magna 3 2.3007 -2.6551, 7.2568

Fathead minnow 2 0.5706 *

AI I of ab()\/ e 5 1.3418** -1.3922, 4.0760

R.sults of RegreSSion Analysis of Fr.shwater Chronic Toxicity versus Hardness

Degr..s of Freedew

......

• Cannot be cal cui ated because degrees of freedan '" O.

** P '" 0.19 for equality of slopes wltn 1 degree of freedan.
W

N

Table 2. (Continued)

Aeute-Chronle Ratio

HardneS5

(119ft es Acute Value Chron Ie Value

Species Caco,) (lIg/U (eS/U .!!!.!.!2.

Cladoceran, 51 1,800 14.17 122.4

DaphnIa magna

Cladoceran, 104- 1,920 123.1 15.60

DaphnIa magna 105

Cladoceran, 205- 4,970 356.6 13.94

Daphn la magna 206

fathead mInnow, 210 27,930· 526.7 53.03

Plmephales promelas

fathead minnow, 44- 5,186 l1l1 217.3 23.87

Plmephales promelas 45

Mysld, 30.ltlt 508 W-.74 5.418

Mysldopsls bahla

• Geometric mean of four values In Table 1.

1111 GeometrIc medn of two values In Table I.

All. SalInity (g/kg).
Table }. Ranked Genus Maan Acute Values wIth SpecIes Mean Acute-Chronlc RatIos

Genus Mean Specl_ Mean Specl_ Mean

Acute Value Acute Value Acute-Chronlc

(..s/u.. SpecIes (..S/U·.. RatIo····

FRESHWATER SPECIES

18 43,250 Banded killifIsh, 43,250

Fundulus dlaphanls

11 40,460 Stonefly, 40,460

Acroneurla Iycorlas

16 30,200 Caddlsfly, 30,200

Unldentlfled sp.

15 21,320 Gold t Ish, 21,320

Carasslus auratus

14 21,200 DMlselfly, 21,200

Un Identl f led sp.

13 14, 100 Worm, 14,100

sp.

w

w 12 13,380 Ra Inbow trout, 13,380

Salma galrdnerl

11 13,000 Amph I pod , 13,000

Gammarus sp.

10 12,770 Sna \I , 12,770

Amnlcola sp.

9 12,180 Amer lean eel, 12,180

AnguIlla rostrata

8 9,839 Common carp, 9,839

Cyprlnus carpIo

7 9,661 Guppy, 9,661

Poecliia retlculata .

6 8,697 Wh 1te perch, 12, 7~

Morone americana

Str lpad bass, 5,914

Morone saxatlils
Teble 1. (ContInued)

Genus ....n SpecIes MNn SpecIes ....n Acute Value Acute Value Acute-Chronlc

(pS/U" SpecIes (ps/U"· RatIo····

5 9,530 Pumpkinseed, 7,544

Lepomls glbbosus

BI ueg III , 12,040

Lepomls macrochlrus

4 8,027 Fathead minnow, 8,027 35.58t

Plmephales promelas

3 4,636 Mayfly, 4,636

Ephemerella subvarta

2 4,312 Rock bass, 4,312

Ambloplltes rupestrls

1,500 CI adoceran, 2,042

Daphnia pullcarla

C Iadoceran, 1,102 29.86tt

Daphn la magna wpo

SALTWATER SPECIES

20 320,000 Soft-shell clam, 320,000

arenarla

19 294,500 Clam, 294,500

Macoma balthlca

18 150,000 Starf Ish, 150,000

Asterlas forbesll

17 149,900 I~umm Ichoq, 149,900

Fundulus heteroclltus

16 n,ooo Mud snail, 72,000

Nassarlus obsoletus

15 70,000 Spot, 70,000

Lelostomus xanthurus

-----~--~ -----
Table 3. (ContInued)

Genus Me8n SpecIes Meen Specl_ ......

Acute Value Acute Value Acute-e....onlc

(pS/U" SpecIes (.g/U"· R.tlo····

14 >50,000 Pol ychaete worm, >50,000

CapItella capltata

13 47,000 HermIt crab, 47,000

Pagurus longlcarpus

12 ~5,OOO Polychaete worm, 49,000

Nerets arenaceodentata

PoIychaete worm, 25,000

Nerels vIreos

11 21,000 Str Iped bass, 21,000

Morone saxatliis

10 17,~90 Atl antIc sllverslde, 7,958

Menldla menldla

Tidewater sllverslde, 38,000

w Menldla penlnsulae

U1

9 17,000 Po

Iychaete worm, 17 ,000

Ctenodrllus serratus

8 18,950 Amphlpod, 18,950

Corophlum volutator

7 11,240 Copepod, 11,240

Eurytemora afflnls

6 6,000 Copepod

, 6,000

Nltocra splnlpes

5 ~,466 Cope pod

, 3,466

Acartla clausl

4 1,180 Eastern oyster, 1,180

Crassostrea vIrgIn lea
Table }. (Continued)

Genus ....n Species Mean Species ...... Acute Value Acute V.lue Acute-Chronlc

("g/U" Species ( ..g/U.... R.tlo····

3 567.5 Mysld, 508 5.478

Mysldopsls bahla

Mys Id, 634

Mysldopsls blgelowl

2 310 Quahog cl am, 310

Mercenarla mercenarla

15\.7 Mysld, 151.7

Heteromysls formosa

- Ranked fran most resistant to most sensItive based on Genus Mean Acute Value.

Inclusion of "greater than" values does not necessarIly Imply a "true ranking,

but does allow use of all genera for whIch data are available so that the

Final Acute Value Is not unnecessarily lowered.

-- Freshwater Genus Mean Acute Values are at hardness = 50 mg/l. w

Q'\

--- From Table 1; freshwater v81 ues are at hardness = 50 mg/l.

---- From Table 2.

t Geometric mean of two val ues In Table 2.

tt Geometr Ic mean of three values In Table 2.
In(Crlterlon Maximum Intercept)

Table]. CCofttlnued)

fresh water

final Acute Value = 1,578 Ilg!L (at hardness = 50 mg!U

criterion Maximum Concentration = <1,578 Ilg/U 12 = 789.0 Ilg/L (at hardness = 50 mg/U

Pooled Slope = 0.8460 (see Table 1)

In<789.0) - I slope x In(50)1

6.6708 - (0.8460 x 3.9120) = 3.3612

Cr Iter Ion Max Imum Concentration = e(0.84601In( hardness) H3.3612)

Final Acute-Chronic Ratio = 17.99 (see text)

Final Chron Ic Va I ue = (l, 578 Ilg!U I 17.99 = 87.72 Ilg/L (at hardness = 50 mg!U

Assumed Chron Ic Slope = 0.8460 (see text)

In(Flnal Chronic Intercept) In(87.72) - Islope x In(50)1

= 4.4741 - (0.8460 x 3.9120) = 1.1645

Final Chronic Value = e(0.84601In(hardness)l+l.1645)

Salt water

final Acute Val us = 149.2 Ilg/L

Criterion Maximum Concentration = 149.2 /2 = 74.fi> IlglL

Final Acute-Chronic Ratio = 17.99 (see text)

Final Chronic Value = (149.2 Ilg/U I 17.99 = 8.293 Ilg/L
Table 4. TOKlcity of Nickel to Aquatic Plants

Hardne••

(Illg/L •• Duration eoncentr.tl..

Species Ch_lcal ~) (day.) Effect hg/U· Reference

FRESHWATER SPECIES

BI ue-green alga, NIckel 14 84% reductIon 600 Spencer and Greene

Anabaena flos-aquae nItrate In gro.rth 1981

BI ue-green alga, NIckel 8 IncIpIent 5 Br Ingmann and Kuhn

Mleroe~stls aeruglnosa chloride Inh 10 ItIon 1918a,b

Green alga, NIckel 10 45% reductIon 5,000 Del/ I Prasad and

Anklstrodesmus falcatus chlorIde In gro.rth 06'11 Prasad 1982

Green 1Ilgll, NIckel 14 98% red uct Ion 100 Spencer and Greene

Anklstrodesmus falcatus nItrllte In growth 1981

Green al ga, NIckel 14 42% reductIon 100 Spencer and Greene

Anklstrodesmus falcatus nItrate In growth 1981

I/ar. aclcularJs

Green al ga, NIckel nitrate or 41.5 12 91 % red uct Ion 100" Hutchinson 19H;

LV Chlamydomonas eugametos "lIe kel su I fate In gro.rth Hutehln9>O and 00 Stokes 1915

Green alga, NIckel nItrate or 41.5 12 53% reductIon 300" HutChInson 1913;

Chlorella I/ulgarls NIckel sulfate In growth Hutch Inson and

Stokes 1975

Green alga, NIckel 10 52% reductIon 5,000 06'11 Prasad and

Chlorococcum sp. chlorIde In growth Del/I Prasad 1982

Green alga, NIckel nItrate or 41.5 12 85% reduct Ion 300" HutChinson 1973;

Haematococcus capensls NIckel sui fate In qro.rth ItJtch I nson and

Stokes 1915

Green alga, NIckel 14 Increased 100 Spencer and Greene

Pedlastrum tetras nitrate growth 1981

Green alga, NIckel nItrate or 47.5 12 54% reductIon 50** Hutch Inson 19H;

Scenedesmus acumlnata NIckel sui fate In growth Hutchinson and

Stokes 1915
rable 4. (Continued)

Species

Green alga,

Scenedesmus acumlnata

Ch8lllical

Nickel nitrate or

Nlcke I sui fate

Hardne.s

(Mg/L as

C~)

47.5

Duration

(days) Effect

13 Reduced

growth

CoRcentratIon

(ps/L)- Reference

500 Stokes et al. 1973;

Hutch Inson and

Stokes 1975

Green alga,

Scenedesmus dlmorphus

Green alga,

Scenedesmus obllquus

Green alga,

Scenedesmus quadrlcauda

Green alga,

Scenedesmus quadrlcauda

Dlatan,

Navicula peiliculosa

Duckweed,

Lemna minor ------

Duckweed,

LeRina minor ------

Macrophyte,

Elodea (Anacharls) canadensis

Nickel

nitrate

NIckel

chi or Ide

NIckel

chlor Ide

Nickel

n ltrate

Nickel

nitrate

Nickel

chloride

Nickel

chloride

14.96

14

10

8

14

14

28

4

28

30~ reduction

In qro~h

47% reduction

In groltt h

Incipient

Inhlb ltlon

60~ reduction

In gro~h

82% reduction

In qro~h

EC50

EC50

(gro~h)

EC50

100

3,000

1,300

100

100

340

450

2,800

Spencer and Greene

1981

Dev I Prasad and

Devl Prasad 1982

Br I ngmann and Kuhn

1977a; 1978a,b;

1979; 1980b

Spencer and Gieene

1981

Fazy et al. 1979

Brown and Rattigan

1979

Wang 1986

Brown and Ratt Igan

1979

Water hyac Inth,

Elchhornla crasslpes

water hyac Inth,

Elchhornla crasslpes

Nickel

chi orlde

Nickel

chloride

12

12

38

38

30~ r~uctlon 4,000

In growth

29% rbductlon 8,000

In qro~h

Mur amoro and Ok I

1984

Mur amoto and Ok I

1964

Giant kelp (young fronds),

Macrocystls pyrlfera

SALTWATER SPECIES

4 EC50 (reduc- 2,000

tlon In

photosynthes I s)

Clendenn Ing and North

1959

• Results are expressed as niCkel, not as the chemical.
Table 5. Bloac;cUlllulaton of Nickel by AquatIc Organ I $liS

Hardn..s

Concentration (Mg/l as Our.tlon

Species Ch_lcel 1n Water (pg/U· CaC!3) (days) Tissue BCF or BAF" Refer,,-cll

FRESHWATER SPECIES

Green alqa. Nickel nitrate or 1.000 6 Whole 9.3 Hutchinson and Stokes

Scenedesmus acumlnata Nickel sulfate body 1975

Water hyac Inth. Nickel 1.000 38 12 Root 256.0 Muramoto and Okl 1984

Elchhornla crasslpes chloride tops 174.2

Water hyacinth, Nickel 4.000 38 12 Root 438.2 Muramoto and Okl 1984

Elchhornla crasslpes chlor Ide tops 500.3

Water hyac Inth. NIckel 8,000 38 12 Root 335.5 Muramoto and Okl 1984

Elchhornla crasslpes chlor Ide tops 576.2

CI adocer an, 63NI In Whole 100 Hall 1978

Daphnia magna O.IM HCI body

CI adocer an, 50 20.1 3.75 Whole 192·" Hall 1982

Daphnia magna body

.p- CI adoceran • 750 20.1 3.75 Whole 123·" Hall 1982

0 Daphnia magna body

Cladoceran, Nickel 58.7 13 Whole 11.6 Watras et al. 1965

Daphn la magna chlor Ide body

Ra Inbow trout, Nickel 1.000 320 180 Muscle 0.8 Cal amar I et al. 1982

galrdnerl chloride

Fathead minnow, Nickel 21 30 Whole 106 LInd et al • Manuscript

Plmephales promelas sulfate body

Fathead minnow, NIckel 44.4 30 Whole 19 LInd at al • Iotinusc rt pt

Plmephales promelas sui fate body

Fathead mInnow. NIckel 108.9 30 Whole 47 LInd et al. Manuscript

Plmephales promelas sulfate body

SALTWATER SPECIES

Rockweed • 1.2 Field Whole 675 t foster 1976

Fucus veslculosls collections plant
Table 5. (Continued)

Hardness

ConceAtrat Ion (.-gIL as Duration

Species Ch.lcal In Water (,g/U- C~) (days) Tissue BCF or BAF" Reference

Brown macroalga, 1.2 FIeld \Jtlo Ie 458.3t Foster \976

Ascophyllum nodosum collections plant

BI ue mussel, NIckel 4.4 84 Soft 4n.7 Zarooglan and Johnson

Mytllus edulls sui fate parts 1984

81 ue mussel, NIckel 10.0 84 Soft 328.6 Zaroogl"n and Johnson

Myt II us edu I Is sui fate parts 1984

Eastern oyster, NIckel 4.2 84 Soft 458.1 Zaroog Ian and Johnson

Crassostrea vlrglnlca sui fate parts 1984

Eastern oyster, NIckel 9.9 84 Soft 261.8 Zaroog Ian and Johnson

Crassostrea vlrglnlca sui fate parts 1984

* Measured concentratIon of nIckel.

1I1l Bloconcentratlon factors (BCFs) and bloaccumulatlon factors (BAFs) are based on measured concentratIons of nIckel In water and In tissue.

Ull Estlmate1 fran graph.

t Factor was converted from dry weIght to wet weight basIs.
Table 6. Other oota on Effectfi of Nlcke. on Aquatic Orga.ls-a

Speclefi

Hardne•• (lIl9Il a.

CoCO) Duration

fRESHWATER SPECIES

Eft.ct

ConcentretIon

(,s/l)· Reference

Alga,

Chlorella pyrenoldosa

Green alga,

Scenedesmus quadrlcauda

Green alga.

Scenedesmus quadrlcauda

Nickel

chlor Ide

NIckel

ammonIum

sui fate

24 hr

96 hr

96hr

Reduced

growth

IncIpIent

Inh Iblt Ion

(rIver water)

Inc Ip lent

InhibitIon

(rIver water)

88

1,500

900

Gerhllrd s lind Wei I er

1977

Br Ingmann and Kuhn

1959a,b

Brlngmann and Kuhn

1959a,b

Alga,

(m h<e:I popu Iat Ion)

Blue-green alga,

Anabaena cyllndrlca

BI ue-green alga,

Anabaena cyllndrlca

NIckel

nItrate

NIckel

sui fate

NIckel

sui fate

87-

99

<53 days

5 days

5 days

Decrease In

dIatom dIversity;

sh 1ft to green and

bl ue-green algae

tb effect on

doubling tIme

(In lIght>

13% re:luctlon In

dOublIng tIme

(In dark)

2-

8.6

15. I

15.1

Patr Ick at al. 1975

Daday et al. 1985

Daday et al. 1985

BI ue-green alga,

Anabaena cyllndrlca

BI ue-green alga,

Anabaena cyllndrlca

BI ue-green II Iga,

Nostoc Iinckla

Blue-green alga,

Nostoc I Inck la

BI ue-green alga,

Nostoc muscorum

Bacter I lI1I,

Aeromonas sobrla

Nickel

chloride

Nickel

chlorIde

NIckel

chlorIde

NIckel

chlorIde

NIckel

chlorIde

Nickel

chloride

40

30 hr

30 hr

24 hr

24 hr

21 days

24 hr**

BCF = 680.5

(In lIght)

BCF = 375.0

(In dark)

EC50 (n I trate

reductIon)

EC50 (ammon la

uptake)

EC50

(surv IVllI)

Reduction In

abundance

1,885

1,14 I

235.1

5

Campbell and SmIth 1986

Campbell and Smith 1986

Kumar at 01. 1985

Kumar et al. 1985

Ral and Ralzada 1985

BabIch and Stotzky

1983
Tabl.6. (contInued)

Hardn.ss

(IIQI'L as CoItcentratlon

Specl.s Ch_Ical CeOO,s) DuratIon Effect ("slL)- R.f......c.

BacterI lJIl. Nickel 40 24 hr** Reduction In 5 Babich and Stotzky

Bac III us brev Is chi or Ide abundance 1983

Bacterium. Nickel 40 24 hrtt* Reduct Ion In 5 Babich and Stotzky

Bac IIIus cereus chloride abundance 1983

Bacterium. Nickel Incipient 100 Br Ingmann and Kuhn

Escher Ich la coil chloride Inhlb Itlon 1959a

Bacter I um. Nickel Incipient 100 Brlngmann and Kuhn

EscherIchIa coil ammonIum Inhibition 1959a

su I tate

Bacter lum. NIckel 16 hr Incipient 2.5 Br Ingmann and Kuhn

Pseudomonas e.utlda chlorIde Inh Iblt Ion n.O) 1917a; 1979; 1980b

BacterllJll. Nickel 40 24 hr** Reduction In 10 Babich and Stotzky

Serratia marcescens chloride abundance 1983

BacterIum. 9 No growth 400 Sato et al. 1986

+-- Nltrosomonas europaea w

Mixed heterotrophic Nickel 0.5 hr ECSO 42.9 Albright et al. 1972

bacter la chlor Ide (survival)

Protozoan. Nickel 72 hr Incipient 140 Br Ingmann 1978;

Entoslphon sulcatum chloride Inhibition Brlngmann and Kuhn

1979; 1980b; 1981

Protozoan. Nickel 28 hr Incipient 50 Br lngmann and Kuhn

Mlcroregma heterostoma chloride Inhibition 1959b

Protozoan. Nickel 28 hr I nc I plent 70 Br I n!J1lann and Kuhn

Mlcroregma heterostoma ,,"mon lum Inhibition 1959b

,sui tate

Protozoan. Nickel 48 hr Incipient 820 8r Ingmann et al. 1980;

Chllomonas paramecium chlor Ide Inhibition Br Ingmann and Kuhn

1981

Protozoan. Nickel 20 hr Incipient 42 Br I ngmann and Kuhn

Uronema parduezl chi or Ide InhibitIon 1980a. 1981
Table 6. (ConttnuecU

Hardness

(.-gil •• Concentration

Species Ch_Ical Ca9C3) Duration Effect c,g/U- Reference

Tub IfIc Id worm, Nickel 34.2 48 hr lGSO 8.70 Brko.llc-Popcwlc and

Tublfex tublfex sui fate 7.00 Popov Ie 19770

GI adoceran, Nickel 48 hr [GSO (r Iver 6,000 Br Ingmann and Kuhn

Daphnia magna chloride water) 1959a,b

GI adoceran, Nickel 48 hr EG50 (r Iver 6,000 Br Ingmann and Kuhn

Daphnia magna CIlImon lum water) 1959a,b

sulfate

CI adoceran, Nickel 288 24 hr EC50 11,000 Br Ingmann and Kuhn

Daphnia magna chlor Ide (swlnrnlng) 1977b

Cladoceran, Nickel 45.3 48 hr [G50 (Immob 11- 1,120 Bles Inger and

Dllphnlll magna chlor Ide zatlon) ( tad) Chr I stensell 1972

CI adoceran , Nickel 45.3 21 days EC50 (Immobll- 130 Bles I nger lind

Daphnia magna chlor Ide zat Ion) Christensen 1972

Cladoceran, Nickel 45.3 21 days 16% reproduc- 30 Bles Inger and

+-- Daphn la magna chloride t Ive Impa Irment Christensen 1972 +--

CI adoceran, Nickel 72 hr BCF = 0.823 1,855 Watras et al. 1985

Daphnia magna chloride BCF = 0.526 1,115

BCF = 1.83 185.5

BCF = 2.20 58.70

BCF = 1.17 18.50

CI Moceran, Nickel 25 48 hr LC50 (TOC = 2,171 LInd et al. Manuscr Ipt

Daphnia pullcarla sui fate 39 mg/L)

Cladoceran, Nickel 28 48 hr LC50 (TOC = 1,140 LInd et al. Manuscript

Daphnia pullcarla sui fate 15 mg/U

Cladoceran, Nickel 28 48 hr LC50 <TOC 1,034 L1nd at al. Manuscr Ipt

Daphnia pullcarla sui fate 13 mg/L)

CI Mocer an, Nickel 29 48 hr LC50 (TOC 697 L1nd at al. Manuscript

Daphnia pullcarla sulfate 13 mq/U
Table 6. (CoAtlnuecU

Hardness

(IIg/L as CoIIC_tret 1011

Species Cta_lcal C~) Duration Effect Cpg/U- Reference

CI adoceran, Nickel 73 48 hr LC50 (rOC = 3,414 Lind et al. Manuscr Ipt

Daphnia pullcarla sui fate 28 mq/L)

CI adoceran, Nickel 74 48 hr LC50 (rOC = 2,325 Lind et al. Manuscrlpt

Daphnia pullcarla sui fate 28 mg/L)

CI adoceran, Nickel 84 48 hr LC50 <TOC 3,014 LInd et al. Manuscript

Daphnia pullcarla sui fa te 32 mg/L)

CI adoceran, Nickel 86 48 hr LC50 (rOC 3,316 LInd et al. Manuscript

Daphnia pullcarla sui fate 34 mg/L)

Cladoceran, Nickel 89 48 hr LC50 <TOC 2,042 LInd et al. Manuscript

Daphnia pullcarla sui fate 18 mg/L)

Cladoceran, Nickel 89 48 hr LC50 <TOC = 2,717 Lind at al. Manuscript

Daphnia pullcarla sulfate 34 mg/L)

Cladoceran, Nickel 100 48 hr LC50 (TOC 3,757 Lind at al. Manuscript

.po Daphnia pullcarla sui fate 34 mg/L)

VI

CI adocaran, Nickel 114 48 hr LC50 <TOC 3,156 Lind et al. Manuscript

Daphnia pullcarla sui fate 27 mg/L)

CI adoceran, Nickel 120 48 hr LC50 <TOC 3,607 Lind et al. Manuscript

DaphnIa pullcarla sulfate 33 mg/L)

Midge, 50 96 hr LC50 8,600 Rahwoldt at al. 1973

Chlronomus sp.

Coho salmon (yearling), Nickel 90 144 hr 100% surv Ivai 5,000 Lorz et al. 1978

Oncorhynchus klsutch chlor Ide

Rainbow trout (0.5-0.9 q) , Nil:: kel 42 48 hr LC50 35,730 WII I ford 1966

galrdnerl sulfate

RaInbow trout (1 yrl. NIckel 240 48 hr LC50 32,000 Brown and Dalton 1970

galrdnerl sui fate
Table 6. (Cont InuecU

Hardness

(Mg/l as Concentrat Ion

Species Che-Ical Cel Duration Effect (,s/U- R.f....enc.

Ra I nbow trout Nickel 104 28 days EC50 (d')dth 50 Birge 1978; Birge and

(embryo, larva) , chlor Ide (92-110) and defonn I ty) Black 1980; Birge et al.

galrdnerl 1978,1979,1980,1981

Ra Inbow trout Nickel 125 28 days a:;50 (death 60 Birge et al. 1981

( embr yo, I arv a) , chlor Ide and defonnlty)

galrdnerl

Ra Inbow trout Nickel 174 28 days 8;50 (death 90 Birge et al. 1981

(embryo, larva) , chlor Ide and de form It y)

galrdnerl

Ra Inbow trout, Nickel 240 3.5 days Decreased gill 2,000 Hughes et al. 1979

Salmo ga Irdner I sui fate d I ffus Ion

Ra Inbow trout (ad 1.11 t) , Nickel 320 6 mo Increase In 1,000 Ar 1110 et al. 1982

galrdnerl chlor Ide liver proteol ytic cx:tlvlty of

males

P- Ra I nbow trout (10 g), Nickel 28.4 20 min Avoidance n.9 Glattlna et al.1982

0' Salmo galrdnerl chloride thresho Id

Ra Inbow trout, Nickel 22.5 48 hr LC50 54,963 Bornatow leI 1983

galrdnerl sui tate

Ra Inbow trout Nickel 50 38 days LC50 1.400 Nebeker et al. 1985

(5 days post hatch), chlor Ide

galrdnerl

Brown trout lO.8-1.2 g) , Nickel 42 48 hr LC50 60,290 Will ford 1966

trutta sui fate

Brook trout (0.4-0.6 g), Nickel 42 48 hr LC50 54,040 Will ford 1966

Salvellnus fontlnalls sulfate

Lake trout (2.5-3.2 g), Nickel 42 48 hr LC50 16,750 Will ford 1966

Salvellnus namaycush sui fate
Table 6. (Continued)

Hardness

(ilg/l as Coftc_tratlOll

Specie. Chellical C~) Duration Effect (Ps/U- R.t......c.

Gold fish, Nickel 19-50 hi" LT 100,000 Ellis 1937

Carass Ius auratus chi orlde 200-210 hr LT 10,000

Goldfish (embryo, larva) , Nickel 195 7 days EC50 (de~th 2,140 BIrge 1978

Carasslus auratus chloride and defonn Ity)

GoldfIsh (embryo, larva) , NIckel 93- 7 days EC50 (de~th 2,780 BIrge and Black 1980;

Carasslus auratus chi orlde 105 and defonn lty) Birge at al. 1981

CaMIOn car p (embryo), Nickel 128 72 hi" LC50 6,100 Blaylock and frank

Cyprlnus carpIo sui fate 1979

Canmon carp (larva), NIckel 128 72 hr LC50 8,460 Blaylock and frank

Cyprl nus carp 10 sui fate 257 hr 750 1979

COlhIIon car p (embryo), Nickel 360 EC50 (ha tch) 22,000 Kap .... and Yadav 1982

Cyprlnus carpIo sui fate

FatheM minnow, NIckel 28 96 hr L.C50 HOC 2,923 LInd at al • Manuscript

Plmephalas promelas sui fate 14 mg/U

.p. Fathead minnow, Nickel 29 96 hr LC50 HOC 2,916 LInd et al. Manuscript -...J

Plmephalas promelas sulfate 12 mg/U

Fathead mInnow, NIckel 71 96 hr LC50 HOC 12,356 LInd at al. Manuscript

Plmephalas promelas sui fate 32 mglL)

Fathead minnow, NIckel 86 96 hr LC50 HOC == 5,}8} LInd et al. Manuscr Ipt

Plmephales promelas sui fate 15 mg/U

fathead mInnow, Nickel 89 96 hr L.C50 HOC 17 ,678 L1nd et al. Manuscript

Plmephales promelas sui fate }} mg/U

fathead mInnow, Nickel 91 96 hr L.CSO HOC 8,617 LInd et 81. Manuscript

Plmephales promelas sulfate }O mglL)

Channel catfIsh (1.2-1.5 g) , NIckel 42 48 hr L.C50 }6,840 WII I ford 1966

Ictalurus punctatus sui fate

Channel catfish, NIckel 93- 7 days 8::50 (death 710 Birge md Black 1980;

Ictalurus punctatus chlor Ide 105 and defonnlty) Birge at al. 1981
Tabl.6. (ContInued)

Hardn.s.

(IIQIL as Ooftc_tratl.

SpecIes Ch_lc.1 Caro,) Duration Effect t,sIU· R.terenc.

Guppy, Nickel 260 96 hi" LC50 (h Igh 34,900 Khangarot 1981

Poect Iia retlculatlll sui fate solids)

Guppy (J 84 mg), Nickel 260 48 hi" LC50 37,000 Khanglllrot at al. 1981

Poecl I I III retlculatlll chloride

BI ueg III (0.7-1.1 g), Nickel 42 48 hr LC50 110,500 Willford 1966

Lepomls macrochlrus sui fate

Largemouth bass Nickel 9,- 8 days EL50 (death 2,020 Birge and Black 1980;

(embryo, I arva) , Chloride 105 and deformity) (2,060) Birge et 1lI1. 1978, 1981

Mlcropterus salmoldes

Narrow-mouthed toad NIckel 195 7 days B:50 (death 50 Btrge 1978; Birge et al.

(embryo, larva), Chloride and deformity) 1979

Gastrophryne carollnensls

Narrow-mouthed toad Nickel 95- 7 days EC50 (dellith 50 Birge and Black 1980

( embryo, I arva) • chlor Ide 103 and deformity)

Gastrophryne caroltnensls

+'-

(Xl fowl er' s toad, Nickel 93- 7 days EC50 (death 11,030 Birge and Black 1980

Bufo fowlerl chloride 105 and deformity)

Marbl ad sa I amander Nickel 93- 8 days ELSO (death 420 Birge and Bhlck 1980;

( embryo. IllIrva), Chloride 105 and deformity) (410) Birge at al. 1978

Ambystomlll opacum
Tebl. 6. (Continued)

S.llnlty Ooncentrat10ft

Spec I•• Ch_lc.1 (g/kg) Ountlon Effect Cps/U- R.ter.c.

SALTWATER SPECIES

Golden bro",," alga, 28 2 days Lowest concen- 500 WlI son and Freeberg 1980

Isochrysls galbana tratlon reduc Ing

chlorophyll -!

Golden bro",," alga, 28 9 days Lowest concen- 80 WII son and Freeberg 1980

Isochrysls galbana tratlon reducing

cell numbers

DI,Hom, Nickel 26 7 days Reduced growth 1,000 Skaar et al. 1974

Phaeodacty I um trlcornutum chloride

DIatom, 14 2 days Chlorophyll 100 WI I son and Freeberg 1980

Thalassloslra~seudonana reduced about

65~ at 12°C

DlatOOl, 14 2 days Chlorophyll a }1 Wilson and Freeberg 1980

Thalassloslra pseudonana ralucal a>ouT

65% at 16·C

+-

\0 Diatom, 14 2 days Chlorophyll 28 WII son and Freeberg 1980

Tha I ass los Ira pseudonana ralucal a>out

65% at 20°C

DlatOOl, 14 2 days Chlorophyll a 17 Wilson and Freeberg 1980

Thalassloslra pseudonana rtd ucad a>ouT

65% at 24·C

DlatOOl, 14 2 days Chlorophyll 80 WII son and Freeberg 1980

Thalassloslra pseudonana red ucad ltlout

65% at 28°C

LJlatOOl, 28 2 days Chlorophyll 12 Wilson and Freeberg 1980

Thalassloslra pseudonana rwucad about

65% at 12·C

DlatOOl, 28 2 days' Chlorophyll 140 WII son and Freeberg 1980

Thalassloslra pS8udonana rwuced about

65S at 16°C
Tabl. 6. (Continued)

Salinity eonc....tnt1011

SfH!CI•• Ch_lcal (g/kg) Duration Effect tes/L)· R.ter....c.

DI~tom, 28 2 days 0'11 orophy I I a 30 WI I son and Fr86berg 1980

Tha I ass los Ira eseudonana reduced abouT

65% at 20·C

Diatom, 28 2 days Chlorophyll a 21 WII!Dn and Freeberg 1980

Thalassloslra eseudonana red uced about

65% at 24·C

Diatom, 28 2 days Chlorophyll a 18 WII son and Freeberg 1980

Thalassloslra eseudonana red uced abouT

65% at 28·C

Diatom, 28 2 days Lowest concen- 100 WII son and Freeberg 1980

Thalassloslra eseudonan~ tratlon reducIng

chlorophyll

oInofl agel late, 28 5 days Reduced chloro- 50 WII son and Freeberg 1980

Glenodlnlum phyll and

populatIon

numbers In chemoVI stat cultures

0

DInoflagellate, 28 2 days Lowest concen- 200 wll son and Freeberg 1980

Glenodlnlum tratlon reduc Ing

chlorophyll

DInot I agel I ate, 28 2 days Chlorophyll 1,000 WII!DO and Freeberg 1980

GymnodInIum splendens reduced about

65% at 16·C

DInoflagellate, 28 2 days Chlorophyll 950 Wll son and Freeberg 1980

GymnodInium splendens reduced cbouT

65% at 20°C

DInofl agel late, 28 2 days Chlorophyll 560 WII son and Freeberg 1980

GymnodinIum splendens reduced about

65% at 24°C
Table 6. (Coatlnued)

SalinIty eo.c.tratl_

Sp!Cles Ch_lcal (g/kg) Duration Effect (Ps/U· Reter.c.

Dlnotl agel late, 26 2 days Chi orophy II 130 WIlson Md Fr eeberg 1960

GymnodInium splendens reduced about

65~ at 26·C

oInot I agel late, 26 2 days Chlorophyl i a 1,800 WlI son and Freeberg 1960

GymnOdInIum splendens red uced l:DouT

65. at 30·C

oInot I agel late, 14 2 days Chlorophyll a 1,800 WII 9:>n and Freeberg 1960

GymnOdinIum splendens reduced abouT

65~ at 16·C

oloot I agel late, 14 2 days Chlorophyll 400 WII9:>R and Freeberg 1960

GymnodinIum splendens reduced about

65% at 30·C

oloot 1agel late, 26 2 days Lowest concen- 200 WII son and Freeberg 1960

GymnOdInIum splendens tratlon reduc log

Chlorophyll

V1 Polychaete worm (adult), Nickel 26 days Inh Iblted 100- Petrich and ReIsh 1979

Ctenodrllus serratus chloride reproduction 500

81 ue mussel, Nickel 29- 10 weeks AlP reduced; no 10 Zaroog I an et al. 1962

Mytl Ius adulls chloride 32 effect on AEC

PClC It Ie oyster (j uven 11 e), Nickel 34 14 days 19% reductIon 20 Watling 1963

Crassostrea chi or Ide In growth

Eastern oyster (larva), NiCkel 24+2 12 days LC50 1,200 Cal abrese et al. 1977

Crassostrea vlrglnlca chloride

Eastern oyster (larva), NIckel 24+2 12 days 54.6. reductIon 1,200 Cal abrese et al. 1917

Crassostrea vlrglnlca chlorIde In growth

Eastern oyster, NIckel 29- 10 weeks etfect on 10 Zarooglan et "I • 1982

Crassostrea vlrglnlca chlor Ide 32 AEC and

canponeots

CI am (I arv a) , NiCkel 35 48 hr Reduced cal c lum 2,000 Ii:> and Zubkott 1983

Mullna lateralls chi or-Ide uptake
Tabl. 6. (Continued)

SalinIty CoIIc...tr.tIOli

SpecIes Ch_lcel (g/kg) Dur.tlon Effect (PaiL)· R.f......ce

Quahog clam (larva), Nickel 24+2 8-10 days LC50 5,700 Cal abre58 et ale 1977

Mercenarla mercenarla chlor Ide No growth 5,700

Common Pacific littleneck NICkel 31 48 hr BCF = 4.3 Hardy and Roesljad I 1982

(adult), nUrate (g III)

Protothaca stamlnea

Common Pac IfIc littleneck Nickel 31 48 hr BCF = 4.0 Hardy and Roesljad I 1982

(adult) , nitrate (whole clam)

Protothaca stamlnea

Copepod (adult), NiCkel 30 n hr LC50 14,570 Luss ler and Cardin 1985

Pseudodlaptomus coronatus chlor Ide

Copepod (ad ul t) , NiCkel 30 n hr LC50 6,006 Lussier and Card In 1985

Acartla clausl chlor Ide

Copepod (ad ul t) , NiCkel 30 n hr LC50 747 LussIer and Card In 1985

Acartla tonsa chloride

\.Jl PInk shr Imp (adul t) , Nickel 48 hr LC50 56,880 Portmann 1968 N Pandalus montagul sui tate

Green crab (adult), NiCkel 48 hr LC50 170,600 Portmann 1968

Ccsrclnus maenas sui fate

Sea urchin (embryo), NiCkel 21 hr Stun ted 7,562 Waterman 1937

Arbacla punctulata Chloride development

Sea urchin (embryo), NICkel 42 hr >50% mortal I ty 7,562 Waterman 1937

Arbacla punctulata chlor Ide

Sea urchin (embryo) , NICkel 18-26 hr Totally 586,900 Tlmour Ian and Watchmaker

Lytechlnus plctus chlor Ide arrested 1972

dElvelopment

Sea urch In (embryo) , NIckel 48 hr Abnonnal 586.9 Tlmour Ian and Watctvnaker

Lytechlnus plctus chloride dElvelopment 1972
eo.centr.tICNI

(,S/L)- R.ferenc.

Tabl. 6. (Continued)

Specl••

Sea ITchln (gCl1lete).

Strongylocentrotus purpuratus

SalInIty

(g/kg) Duration

300 min

Effect

Depressed spem

mot \I lty

58.69 Tlmourlan and watchmaker

1971

• Resul ts are EDCpressed as nIckel. not as the cham Ical •

Vt

W

•• I ncubated for 2 to 4 days atter El>Cposure.
REFERENCES

Abbe, G.R. 1982. Growth, mortality and copper-nickel accumulation by oysters

(Crassostrea virginica) at the ~~rgantown steam electric station on the

Potomac River, ~1aryland. J. Shellfish Res. 2:3-13.

Abo-Rady, t-f. 1979. The levels of heavy metals (Cd, Cu, Hg, Ni, Pb, Zn) in

brook trouts from the River Leine in the area of Gottingen (West Germany). Z.

Lebensm. Unters. Forsch. 168:259-263.

Agrawal, S.J., A.K. Srivastava and H.S. Chaudhry. 1979. Haematological

effects of nickel toxicity on a fresh water teleost, Colisa fasciatus. Acta

Pharmacol. Toxicol. 45:215-217.

Ahsanullah, t1. 1982. Acute toxicity of chromium, mercury, molybdenum, and

nickel to the amphipod Allorchestes compressa. Aust. J. Mar. Freshwater Res.

33:465-474.

Albright, L.J., J.\J. i-lentworth and La. Wilson. 1972. Technique for measuring

metallic salt effects upon the indigenous heterotrophic microflora of a

natural water. Water Res. 6:1589-1596.

Alman, H. and P. Boger. 1984. ~ickel-dependent uptake-hydrogenase activity in

the blue-green alga Anabaena variabilis. Z. Naturforsch. 39C:90-92.

54
Amemiya, Y. and O. Nakayama. 1984. The chemical composition and metal

ab30r?tion capacity of the sheat~1':::..:tGria15 isolated f:ow. :·1icrocystis,

cyanobacteria. Jpn. J. Limnol. 45:187-193.

Anderson, B.G. 1948. The apparent thresholds of toxicity to Daphnia magna for

chlorides of various metals when added to Lake Erie water. Trans. Am. Fish.

Soc. 78:96-113.

Anderson, D.R. 1981. The combined effects of nickel, chlorine, and

temperature on the mortality of rainbow trout, Salmo gairdneri. Ph.D. thesis.

University of Washington, Seattle, \JA. Available from: University ~1icrofilms,

Ann Arbor, ~1I. Order :lo. 8121178.

Anderson, D.R. 1983. Chlorine-heavy metals interaction on toxicity and metal

accumulation. In: \~ater chlorination: Environmental impact and health

effects. Vol. 4, Book 2. Jolley, R.Le, r,J.A. 3rungs, J.A. CotrtNo, R.B.

Cumming, J.S. l1attice and V.A. Jacobs (Eds.). Ann Arbor Science Publishers,

Ann Arbor, HI. pp. 811-826.

Anderson, P.D. 1973. An approach to the study of aultiple toxicity through

the derivation and use of quantal response curves. Ph.D. thesis. Oregon State

University, Corvallis, OR. Available from: University flicrofilms, Ann Arbor,

:11. Order No. 74-4187.

Anderson, P.O. and L.J. Heber. 1975. Toxic response as a quantitative

function of body size. Taxicol. Appl. Pharmacal. 33:471-483.

55
Applegate, V.C., J.R. Howell, A.E. Hall, Jr. and M.A. Smith. 1957. Toxicity

of 4,346 chemicals to larval lampreys and fishes. Special Scientific Report--

Fisheries No. 207. U.S. Fish and Wildlife Service, Washington, DC.

Arillo, A., C. Margiocco, F. lielodia and P. Mensi. 1982. Biochemical effects

of long term exposure to Cr, Cd, Ni on rainbow trout (Salmo gairdneri Rich.):

Influence of sex and season. Chemosphere 11:47-57.

Babich, H. and G. Stotzky. 1983. Temperature, pH, salinity, hardness, and

particulates mediate nickel toxicity to eubacteria, an actinomycete, and

yeasts in lake, simulated estuarine, and sea waters. Aquat. Toxicol.

3:195-208.

Babich, H. and G. Stotzk.y. 1985. Heavy metal toxicity to microbe-mediated

ecologic processes: A review and potential application to regulatory

policies. Environ. Res. 36:111-137.

Babich, H., C. Shopsis and E. Borenfreund. 1986. In vitro cytotoxicity

testing of aquatic pollutants (cadmium, copper, zinc, nick.el) using

established fish cell lines. Ecotoxicol. Environ. Safety 11-:91-99.

Bailey, R.C. and P.M. Stokes. 1985. Evaluation of filamentous algae as

biomonitors of metal accumulation in softwater lakes: A multivariate

approach. In: Aquatic toxicology and hazard assessment: 7th symposium.

Cardwell, R.D., R. Purdy and R.C. Bahner (Eds.). ASTM STP 854. American

Society for Testing and Materials, Philadelphia, PA. pp. 5-26.

56
Ballester, A. and J. Castellvi. 1979. Contribution to the biokinetic study of

vanadium and nickel uptake by marine organisms. Invest. Pesq. 43:449-478.'

Baudouin, M.F. and P. Scoppa. 1974. Acute toxicity of various metals to

freshwater zooplankton. Bull. Environ. Contam. Toxicol. 12:745-751.

Bean, B. and A. Harris. 1977. A calcium-reversible selective inhibition of

flagellar coordination by nickel ion in Chlamydomonas. Abstracts of the

annual meeting of the American Society of Microbiology.

Becker, C.D. and M.G. Wolford. 1980. Thermal resistance of juvenile salmonids

sublethally exposed to nickel, determined by the critical thermal maximum

method. Environ. Pollute (Series A) 21:181-189.

Bengtsson, B. 1978. Use of a harpacticoid copepod in toxicity' tests. Mar.

Pollute Bull. 9:238-241.

Besser, J.M. 1985. Bioavailability and toxicity of heavy metals in mine

tailings leachate to ~q~a~ic invertebrates. M.S. thesis. University of

Missouri, Columbia, MS.

Biddinger, G.R. and S.P. Gloss. 1984. The importance of trophic transfer in

bioaccumulation of chemical contaminants in aquatic ecosystems. Residue Rev.

91:103-145.

Biesinger, K.E. and G.M. Christensen. 1972. Effect of various metals on

survival, growth, reproduction, and metaabolism of Daphnia magna. J. Fish.

Res. Board Can. 29:1691-1700.

57
Birge, W.J. 1978. Aquatic toxicology of trace elements and coal and fly ash.

In: Energy and environmental stress in aquatic systems. Thorp, J.H. and J.W.

Gibbons (Eds.). CONF-771114. National Technical Information service,

Springfield, VA. pp. 219-240.

Birge, W.J. and J.A. Black. 1980. Aquatic toxicology of nickel. In: Nickel in

the environment. Nriagu, J.O. (Ed.). Wiley, New York, NY. pp. 349-366.

Birge, W.J., J.E. Hudson, J.A. Black and A.G. Westerman. 1978. Embryo-larval

bioassays on inorganic coal elements and in situ biomonitoring of coal-waste

effluents. In: Surface mining and fiSh/wildlife needs in the eastern United

States. Samuel, D.E., J.R. Stauffer, C.H. Hocutt and W.T. Mason (Eds.).

PB298353. National Technical Information Service, Springfield, VA. pp.

97-104.

Birge, W.J., J.A. Black and A.G. Westerman. 1979. Evaluation of aquatic

pollutants using fish and amphibian eggs as bioassay organisms. In: Animals

as monitors of environmental pollutants. Neilson, S.W., G. ~ligaki and D.G.

Scarrelli (Eds.). National Academy of Sciences, Washington, DC. pp. 10~-118.

Birge, W.J., J.A. Black, A.G. Westerman and J.E. Hudson. 1980. Aquatic

toxicity tests on inorganic elements occurring in oil shale. In: Oil shale

symposium: Sampling, analysis and quality assurance. Gale, C. (Ed.).

PB80-221435 or EPA-600/9-80-022. National Technical Information Service,

Springfield, VA. pp. 519-534.

58
Birge, W.J., J.A. Black, and B.A. Ramey. 1981. The reproductive toxicology of

aquatic contaminants. In: Hazard assessment of chemicals: Current

developments. Vol. 1. Saxena, J. and F. Fisher (Eds.). Academic Press, New

York, NY. pp. 59-115.

Blaise, C. and P. Couture. 1984. Dection with the aid of bioassay

(Selenastrum capricornutum) of the effects of trace metals in the aquatic

environment. Toxicity or enrichment by essential nutrients. Hydrobiologia

114:39-50.

Blaylock, B.G. and ~1.L. Frank. 1979. A comparison of the toxicity of nickel

to the developing eggs and larvae of carp (Cyprinus carpio). Bull. Environ.

Contam. Toxicol. 21:604-611.

Bornatowicz, ~. 1983. Assessment of the acute toxicity of nickel sulfate to

rainbow trout. PB84232073. ~ational Techn~cal Information Service,

Springfield, V~. "

Bosserman, R.IJ. 1985. Distribution of heavy metals in aquatic oacrophytes

from Okefenokee swamp. Symp. Biol. Hung. 29:31-40.

Bradley, R.W. and J.R. ~brris. 1986. Heavy metals in fish from a series of

metal-contaminated lakes near Sudbury, Ontario. Water Air Soil Pollute

27:341-354.

59
BraginskiYt L.P. and E.P. Shcherban. 1978. Acute toxicity of heavy metals to

aquatic invertebrates at different temperatures. Hydrobiol. J. 14(6) :78-82.

Brezina t E.R. and M.l. Arnold. 1977. Levels of heavy metals in fishes from

selected Pennsylvania waters. Publication No. SO. Pennsylvania Department of

Environmental Resources t Bureau of Water Quality i~nagementt Harrisburg t PA.

Bringmann t G. 1978. Determination of the biological toxicity of waterbound

substances to~.ards protozoa. I. Bacteriovorous flagellates (model organism:

Entosiphon sulcatum Stein). Z. Wasser Abwasser Forsch. 11:210-215.

Bringmann t G. and R. Kuhn. 1959a. The toxic effects of waste water on aquatic

bacteria t algae t and small crustaceans. Gesund.-Ing. 80:115-120.

Bringmann, G. and R. Kuhn. 1959b. Water toxicology studies with protozoans as

test organisms. Gesund.-Ing. 80:239-242.

Brin~mann, G. and R. Kuhn. 1977a. Limiting values for the damaging action of

water pollutants to bacteria (Pseudomonas putida) and green algae

(Scenedesmus guadricauda) in the cell multiplication inhibition test. Z.

Wasser Abwasser Forsch. 10:87-98.

Bringmann t G. and R. Kuhn. 1977b. Results of the damaging effect of water

pollutants on ~aphnia magna. Z. Wasser Abwasser Forsch. 10:161-166.

60
Bringmann, G. and R. Kuhn. 1978a. Li~iting values for the noxious effects of

W<Tter poD utant mateti/al to "b1tle algae C!icrocystis' a·E'·~'..!g:'·~osa; and green

algae (Scenedesmus guadricauda) in cell propagation inhibition tests. Vom

Wasser 50:45-60.

Bringmann, G. and R. Kuhn. 1978b. Testing of substances for their toxicity

threshold: Model organisms Microcystis (Diplocystis) aeruginosa and

Scenedesmus quadricauda. [utt. Int. Ver. Theor. Angew. Limnol. 21:275-284.

Bringmann, G. and R. Kuhn. 1979. Comparison of toxic limiting concentrations

of water conta~ination toward bacteria, algae and protozoa in the cell-growth

inhib ition test. Haustech. Bauphys. Umwel t tech. 100: 249-252.

Bringmann, G. and R. Kuhn. 1980a. Determination of the harmful biological

effect of water pollutants on protozoa. II. Bacteriovorous ciliates. Z.

Wasser Abwasser Forsch. 13:26-31.

Bringmann, G. and R. Kuhn. 1980b. Comparison of the toxicity thresholds ot

water pollutants to bacteria, algae, and protozoa in the cell multiplication

inhibition test. Water Res. 14:231-241.

Bringmann, G. and R. Kuhn. 1981. Comparison of the effects of harmful

substances on flagellates as well as ciliates and on halozoic bacteriophagous

and saprozoic protozoa. Gas-Wasserfach, Wasser-Aowasser 122:308-313.

61
Bringmann, G. and R. Kuhn. 1982. Results of toxic action of water pollutants

on Daphnia magna Straus tested by an improved standardized procedure.

Wasser Abwasser Forsch 15:1-6.

Bringmann, G., R. Kuhn and A. \Jinter. 1980. Determination of biological

lJ. "'

damage from water pollutants to protozoa. III. Saprozoic flagellates. Z.

Waasser Abwasser Forsch. 13:170-173.

Brkovic-Popovic, 1. and rt. Popovic. 1977a. Effects of heavy metals on

survival and respiration rate of tubificid worms: Part I - Effects on

survival. Environ. Pollute 13:65-72.

Brkovic-Popovic, I. and M. Popovic. 1977b. ~ffects of heavy metals on

survival and respiration rate of tubificid worms: Part II - Effects on

respiration rate. Environ. Pollute 13:93-98.

Brown, B.T. and B.H. Rattigan. 1979. Toxicity of soluble copper dnd uther

metal ions to Elodea canadensis. Environ. Pollute 20:303-314.

Brown, V.M. 1968. The calculation of the acute toxicity of mixtures of

poisons to rainbow trout. Water Res. 2:723-733.

Brown, V.M. and R.A. Dalton. 1970. The acute lethal toxicity to rainbow trout

of mixtures of copper, phenol, zinc and nickel. J. Fish Biol. 2:211-216.

62
Bryan, G.W., W.J. langston, L.G. Hummerstone , G.R. Burt and Y.B. Ho. 1983. An

assessment of the gastropod, Littorina littorea, as an indicator of heavy

metal contamination in United Kingdom estuaries. J. l~r. Bioi. Assoc. U.K.

63:327-345.

Bryant, V., O.M. Newberry, A.S. McLusky and R. Campbell. 1985. Effect of

temperature and salinity on the toxicity of nickel and zinc to two estuarine

invertebrates (Corophium volutator, Macoma balthica). Mar. Ecol. Prog. sere

24: 139-153.

Buikema, A.L., Jr •• J. Cairns, Jr. and G.W. Sullivan. 1974a. Rotifers as

monitors of heavy metal pollution in water. Bulletin 71. Virginia Water

Resources Research Center, Blacksburg, VA.

Buikema, A.L., Jr., J. Cairns, Jr. and G.W. Sullivan. 1974b. Evaluation of

Philodina acuticornis (Rotifera) as a bioassay organism for heavy metals.

Water Resour. Bull. 10:648-661.

Buikema, A.L., Jr., C.L. see and J. Cairns, Jr. 1977. RotHer sensitivity to

combinations of inorganic water pollutants. Bulletin 92. _Virginia Water

Resources Research Center, Blacksburg, VA.

63
Cairns, J., Jr., K.W. Thompson and A.C. Hendricks. 1981. Effects of

fluctuating, sublethal applications of heavy metal solutions upon the gill

ventilation response of bluegills (Lepomis macrochirus). EPA-600/3-81-003.

National Technical Information Service, Springfield, VA.

Calabrese, A. and D.A. Nelson. 1974. Inhibition of embryonic development of

the hard clam, Hercenaria rnercenaria by heavy metals. Bull. Environ. Contam.

Toxicol. 11:92-97.

Calabrese, A., R.S. Collier, D.A. Nelson and J.R. ~lacInnes. 1973. The

toxicity of heavy metals to embryos of the American oyster Crassostrea

virginica. ~lar. Bioi. (Berl.) 18: 162-166.

Calabrese, A., J.R. ~clnnes, D.A. Nelson and J.E. tUller. 1977. Survival and

growth of bivalve larvae under heavy-metal stress. tlar. Biol. (Berl.)

41:179-184.

Calamari, D., G.F. Gaggino and G. Pacchetti. 1982. Toxicokinetics of low

levels of Cd, Cr, Ni and their mixture in long-term treatment on Salmo

gairdneri Rich. Chemosphere 11:59-70.

Call, D.J., L.T. Brooke, N. Ahmad and J.E. Richtar. 1983. Toxicity and

metabolism studies with EPA priority pollutants and related chemicals in

freshwater organisms. PB83263665 or EPA-600/3-83-095. National Technical

Information Service, Springfield, VA.

64
Callahan, M.A., M.W. Slimak, N.I,J. Gabel, loP. :'1ay, C.F. Fowler, J.R. Freed,

P. Jennings, R.I.. Durfee, :.C. 1;;'1:.t:T,o're, B. !·!aestri., \!.R. ~t3:bey, B.R. Holt

and C. Gould. 1979. Water-related environmental fate of 129 priority

pollutants. Vol I. EPA-440/4-79-029a. National Technical Information Service,

Springfield, VA. pp. 15-1 to 15-9.

Campbell, P.M. and G.D. Smith. 1986. Transport and accumulation of nickel

ions in the cyanobacterium Anabaena cylindrica. Arch. Biochem. Biophys.

244:470-477.

Cardin, J.A. 1985. u.S. EPA, Narragansett, RIo U1ernorandum to D.J. Hansen.

U.S. EPA, Narragansett, RI.)

Chapman, G.A., S. Ota and F. Recht. ~lanuscript. Effects of water hardness on

the toxicity of metals to Daphnia magna. U.S. EPA, Corvallis, OR.

Chapman, P.M. 1985. Effects of gut sediment contents on measurements of ~etdl

levels in benthic invertebrates - a cautionary note. Bull. Environ. Contam.

Toxicol. 35:345-347.

Chapman, W.H., H.L. Fisher and M.W. Pratt. 1968. Concentration factors of

chemical elements in edible aquatic organisms. UCRL-50564. National Technical

Information Service, Springfield, VA.

Chassard-Bouchard, C. and G. Balvay. 1978. Application of electron probe

x-ray microanalysis to the detection of metal pollutants in freshwater

zooplankton. Hicrosc. Acta (Suppl.) 2:185-192.

65
Chaudhry, H.S. 1984. Nickel toxicity on carbohydrate metabolism of a

freshwater fis~, Colisa fasciatus. Toxicol. Lett. 20:115-121.

Chaudhry, H.S. and K. Nath. 1985. Nickel induced hyperglycemia in the

freshwater fish, Colisa fasciatus. Water Air Soil Pollute 24:173-176.

Chaudry, H.S. and K. Nath. 1985. Effect of nickel intoxication on liver

glycogen of a freshwater teleost. Colisa fasciatus. Acta Hydrochim.

Hydrobiol. 13:245-248.

Cherry, D.S., R.K. Guthrie, F.F. Sherberger and S.R. Larrick. 1979. The

influence of coal ash and thermal discharges upon the distribution and

bioaccumulation of aquatic invertebrates. Hydrobiologia 62:257-267.

Christensen, E.R., C.Y. Chen and J. Kannall. 1985. The response of aquatic

organisms to mixtures of toxicants. Water Sci. Technol. 17:1445-1446.

Clendenning, K.A. and W.J. North. 1959. Effects of wastes on the giant kel?,

Macrocystis pyrifera. In: Effects of wastes on the giant kelp, aacrocystis

pyrifera. Pearson, E.A. (Ed.). Proceedings of the first international

conference on waste disposal in the marine environment, Berkeley, CA.

Cowgill. V.M •• H.W. Emmel and I.T. Takahashi. 1985. Inorganic chemical

composition of trout food pellets and alfalfa used to sustain Daphnia magna

Straus. Bull. Environ. Contam. Toxicol. 34:890-896.

66
Cowgill, U.M., H.W. ~el, D.L. Hopkins, S.L. Applegath and I.T. Takahashi.

1986. The influence of water on repro~uctiv~ success and chemical co~position

of laboratory reared populations of Daphnia magna. Water Res. 20:317-323.

Daday, A., A.H. Mackerras and G.D. Smith. 1985. The effect of nickel on

hydrogen metabolism and nitrogen fixation in the cyanobacterium Anabaena

cylindrica. J. Gen. HicrobioL 131:231-238.

Dallinger, R. and H. Kautzky. 1985. The importance of contaminated food for

the uptake of heavy metals by rainbow trout (Salmo gairdneri): A field study.

Oegologia 67: 82-89.

Devi Prasad, P.V. and P.S. Devi Prasad. 1982. Effect of cadmium, lead and

nickel on three freshwater green algae. Water Air Soil Pollute 17 :263-268.

Dixon, H.J. and :1.8. 3rown (Eds.). 1979. B~1DP Biomedical Computer Progra::as,

P-series. University of California, Berkeley, CA. p. 521.

Dorfman, D. 1977. Tolerance of Fundulus heteroclitus to different metals in

salt water. Bull. N.J. Acad. Sci. 22:21-23.

Doudoroff, P. 1956. Some experiments on the toxicity of complex cyanides to

fish. Sewage Ind. \.Jastes. 28:1020-1026.

67
Doudoroff, P. and M. Katz. 1953. Critical review of literature on the

toxicity of industrial wastes and their components to fish. II. The metals,

as salts. 25:802-839.

Doudoroff, P., G. Leduc and C.R. Schneider. 1966. Acute toxicity to fish of

solutions containing complex metal cyanides, in relation to concentrations of

molecular hydrocyanic acid. Trans. :\m. Fisb. Soc. 95:6-22.

Dugan, P.R. 1975. Bioflocculation and the accumulation of chemicals by

floc-forming organisms. EPA 600/2-75-032. National Technical Information

Service, Springfield, VA.

Dunstan, J.C., A. deForest and R.W. Pettis. 1980. Mytilus edulis as an

indicator of trace metal pollution in naval dockyard waters with preliminary

results from Williamstown Naval Dockyards, Victoria. MRL-R-78l. Department of

Defense, Materials Research Laboratories, Melbourne, Victoria, Canada.

Eisler, R. 1977a. Acute toxicities of selected heavy metals to the soft-shell.

clam, Mya arenaria. Bull. Environ. Con tam. Toxicol. 17:137-145.

Eisler, R. 1977b. Toxicity evaluation of a complex metal mixture to the

softshell clam Mya arenaria. Mar. Biol. (Berl.) 43:265-276.

Eisler, R. 1981. Trace metal concentrations in marine organisms. Pergamon

Press, New York, NY.

Eisler, R. and R.J. Hennekey. 1977. Acute toxicities of Cd+2, Cr+6 ,

Hg+2, Ni+2 and Zn+2 to estuarine macrofauna. Arch. Environ.

Contam. Toxicol. 6:315-323.

68
Eisler, R., M.~1. Barry, R.I. Lapan, Jr., G. Telek, E.\~. Davey and A.Eo Soper.

1973. Metal survey of the't::a::-ine clam pita!:' morrhauna collected near a ~hode

Island (USA) electroplating plant. Mar. BioI. (Berl.) 45:311-317.

Ellis, H.M. 1937. Detection and measurement of stream-pollution. Bulletin No.

22. Bureau of Fisheries, U.S. Department of Commerce, Washington, DC.

Fezy, J.S., D.F. Spencer and R.\~. Greene. 1979. The effect of nickel on the

growth of the freshwater diatom tlavicula pelliculosa. Environ. Pollut.

20:131-137.

Forstner, U. 1984. :'1etal pollution of terrestrial waters. In: Changing metal

cycles and human health. ~riagu, J.O. (Ed.). Springer-Verlag, New York, NY.

pp. 71-94.

Foster, P. 1976. Concentration and concentration factors of heavy metdls in

brown algae. Environ. Pollute 10:9-17.

Gentile, J.H., S.U. Gentile, N.G. Hairston, Jr. and B.K. Sullivan. 1982. The

use of life-tables for evaluating the chronic toxicity of pollutants to

Mysidopsis bahia. Hydrobiologia 93:179-187.

Gerhards, U. and H. \~eller. 1977. The uptake of mercury, cadmium and nickel

by Chlorella pyrenoidosa. Z. Pflanzenphysiol. 82:292-300.

69
Giattina, J.D., R.R. Garton and D.G. Stevens. 1982. Avoidance of copper and

nickel by rainbow trout as monitored by a computer-based data acquisition

system. Trans. Am. Fish. Soc. 111:491-504.

Gill, T.S. and J.C. Pant. 1981. Toxicity of nickel to the fish Puntius

conchonius (Ham.) and its effects on blood glucose and liver glycogen. Compo

Physiol. Ecol. 6:99-102.

Gordon, i1., G.A. Knauer and J.H. t'1artin. 1980. Mytilus californianus as a

bioindicator of trace metal pollution: Variability and statistical

considerations. r~r. Pollute Bull. 11:195-198.

Grande, M. and S. Andersen. 1983. Lethal effects of hexavalent chromium, lead

and nickel on young stages of Atlantic salmon (Salmo salar L.) in soft water.

Vat ten 39:405-416.

Guilizzoni, P. 1980. Heavy metals distribution and their effects on

pho tosynthetic rates of two submerged macrophytes of Lake Hezzola. In:

Environment and quality of life. Second environmental research programme

1976-1980. EUR-6388 EN. ISBN 92-825-0496-4. Commission of the European

Communities, Brussels, Luxembourg. pp. J4-38.

Hale, J.G. 1977. Toxicity of metal mining wastes. Bull. Environ. Contam.

Toxicol. 17 :66-73.

70
Hall, R.A., E.G. Zook and G.t1. :'1eaburn. 1973. National :larine Fisheries

Service survey of trace elements in the fishery resource. NOAA Technical

Report ill1FS SSRF-721. National Technical Information Service, Springfield, VA.

Hall, T. 1978. Nickel uptake, retention and loss in Daphnia magna. M.S.

thesis. University of Toronto, Toronto, Ontario, Canada.

Hall, T.M. 1982. Free ionic nickel accumulation and localization in the

freshwater zooplankter, Daphnia magna. Limnol. Oceanogr. 27:718-727.

Hansen, D.J. 1983. U.S. EPA, Gulf Breeze, FL. (~emorandum to \l.A. Brungs.

U.S. EPA, Narragansett, RI.)

Hardy, J.T. and G. Roesijadi. 1982. Bioaccumulation kinetics and oxygen

distribution of nickel in the marine clam Protothaca staminea. Bull. Environ.

Contam. Toxicol. 23:566-572.

Havas, a. and T.C. nutchinson. 1982. Aquatic invertebrates from the Smoking

Hills, N.ILI.: Effect of pH and metals on mortality. Can. J. Fish. Aquat.

Sc 1. 39: 890-903.

Heit, M. and C.S. Klusek. 1985. Trace element concentrations in the dorsal

muscle of white suckers and brown bullheads from two acidic Adirondack lakes.

Water Air Soil Pollute 25:87-96.

Ho, ~.S. and P.L. Zubkoff. 1983. The opposing effects of cadmium and nickel on

calcium uptake by larvae of the clam Xulinia lateralis. Compo Biochem.

Physiol. 74C :337-339.

71
Hughes, G.M., S.F. Perry and V.M. Brown. 1979. A morphometric study of

effects of nickel, chromium aDd cadmium on the secondary lamellae of rainbow

trout gills. water Res. 13:665-679.

Hutchinson, N.J. and J.B. Sprague. 1983. Chronic toxicity of a mixture of 7

metals to flagfish in soft, acid water. In: Proceedings of the eighth annual

aquatic toxicity workshop. Kaushik, N.K. and K.R. Solomon (Eds.). Canadian

Technical Report of Fisheries and Aquatic Sciences No. 1151. Fisheries and

Oceans, Ottawa, Ontario, Canada. p. 191.

Hutchinson, J.N. and J.B. Sprague. 1986. Toxicity of trace metal mLxtures to

American flagfish (Jordanella floridae) in soft, acidic water and

implications for cultural acidification. Can. J. Fish. Aquat. Sci.

43:647-655.

Hutchinson, T.C. 1973. Comparative studies of the toxicity of heavy metals to

phytoplankton and their synergistic interactions. Water Pollute Res. Can.

8:68-90.

Hutchinson, T.C. and P.M. Stokes. 1975. Heavy metal toxicity and algal

bioassays. In: Water quality parameters. Barabas, S. (Ed.). ASIM STP 573.

American Society for Testing and Materials, Philadelphia, PA. pp. 320-343.

Hutchinson, T.C., A. Fedorenko, J. Fitchko, A. Kuja, J. Van Loon and J.

Lichwa. 1975. MOvement and compartmentation of nickel and copper in an

aquatic ecosystem. In: Trace substances in environmental health - IX.

Hemphill, D.O. (Ed.). University of tftssouri, Columbia, MO. pp. 89-105.

72
Janauer. G.A. 1985. Heavy metal accumulation and physiological effects on

--<\uS't~ian 'macrophytes. Symp. Biol. -Hung. 29: 21-30.

Jay. F.B. and R.J. Uuncy. 1979. Toxicity to channel catfish of wastewater

from an Iowa coal beneficiation plant. Iowa State J. Res. 54:45-50.

Jenkins. D.W. 1980. Biological monitoring of toxic trace metals. Vol. 2:

Toxic trace metals in plants and animals of the world. Part III.

EPA-600/3-80-0n or PB81-103509. National Technical Information Service.

Springfield, VA.

Jennett, J.C•• J.E. Smith and J.M. Hassett. 1982. Factors influencing metal

accumulation by algae. EPA-600/2-82-100. ~ational Technical Information

Service. Springfield. VA.

Jones, J.R.E. 1935. The toxic action of heavy metal salts on the three-spined

stickleback (Gasterosteus aculeatus). J. Exp. BioL 12:165-173.

Jones, J.R.E. 1939. The relation between the electrolytic solution pressures

of the metals and their toxicity to the stickleback (Gasterosteus aculeatus

L.). J. Exp. Biol. 16:425-437.

Kaiser. K.L.E. 1980. Correlation and prediction of metal toxicity to aquatic

biota. Can. J. Fish. Aquat. Sci. 37:211-218.

73
Kanai, K. and H. Wakabayashi. 1984. Purification and some properties of

protease from Aeromonas hYdrophila. Bull. Jpn. Soc. Sci. Fish. 50:1367-1374.

Kapur, K. and N.A. Yadav. 1982. !he effects of certain heavy metal salts on

the development of eggs in common carp, Cyprinus carpio var. communis. Acta

Hydrochim. Hydrobiol. 10:517-522.

Kawamata, 5., Y. Yamauro, H. Hayashi and S. Komiyama. 1983. Contents of heavy

metals in fishes in Nagano prefecture. CA Selects: Environ. Pollute Issue

7:4. Abstr. No. 98:105850d, 1983.

Keller, W. and J.R. Pitblado. 1984. Crustacean plankton in northeastern

Ontario lakes subjected to acidic deposition. Water Air Soil Pollute

23:27-291.

Khangarot, B.S. 1981. Lethal effects of zinc and nickel on freshwater

teleosts. Acta Hydrochim. Hydrobiol. 9:297-302.

Khangarot, B.S., V.S. Durve and V.K. Rajbanshi. 1981. Toxicity of

interactions of zinc-nickel, copper-nickel and zinc-nickel-copper to a

freshwater teleost, Lebistes reticulatus (Peters). Acta Hydrochim. Hydrobiol.

9:495-503.

Khangarot, B.S., S. Mathur, and V.S. Durve. 1982. Comparative toxicity of

heavy metals and interaction of metals on a freshwater pulonate snail Lymnaea

acuminata (Lamarck). Acta Hydrochim. Hydrobiol. 10:367-375.

74
Kissa, E., M. Moraitou-Apostolopoulou and V. Kiortsis. 1984. Effects of four

heavy metals on survival. a::id hatching of Artemia sal.ina (L.). Arc~....

Hydrobiol. 102:255-264.

Kopp, J.F. and R.C. Kroner. 1967. Trace ~etals in waters of the United

States, Oct. 1, 1962, to Sept. 30, 1967. Federal Water Pollution

Administration, Cincinnati, OH.

Kumar, D., ~. Jha and H.D. Kumar. 1985. Heavy-metal toxicity in the

cyanobacterium ~ostoc linckia. Aquat. Bot. 22:101-105.

La Touche, Y.D. and ~1.C. ~x. 1982. Seasonal variations of arsenic and other

trace elements in bay mussels 01ytilus edulis). Bull. Environ. Contam.

Toxicol. 29:665-670.

Lazareva, L.P. 1985. Changes in biological characteristics of Daphnia magna

from chronic action of copper and nickel at low concentrations. Hydrobiol. J.

21(5) :59-62.

LeBlanc, G.A. 1984. Interspecies relationships in acute toxicity of chemicals

to aquatic organisms. Environ. Toxicol. Chern. 3:47-60.

Lewis, ~1.A. 1986. I~pact of municipal wastewater effluent on water quality,

periphyton, and invertebrates in the Little tiiami River near Xenia, Uhio.

Ohio J. Sci. 86:2-8.

75
Lind, D., K. Alto and S. Chaltterton. Manuscript. Regional copper-nickel

study: Aquatic toxicological study. Minnesota Environmental 4uality Board,

Minneapolis, MN.

Lopez-Avila, V., W.D. M:Kenzie, W.W. Sutton, R. Kaminsky, U. Spanagel, T.A.

Olsson and J.R. Taylor. 1985. Application of chemical fractionation/aquatic

bioassay procedure to hazardous waste site monitoring. EPA-600/4-85-o59 or

PB86-109493. National Technical Information Service, Springfield, VA.

Lorz, H.W., R.H. Williams and C.A. Fustish. 1978. Effects of several metals

on smol ting of coho salmon. EPA-600/3-73-090. National Technical Information

Service, Springfield, VA.

Lussier, S.M. and J.A. Cardin. 1985. u.S. EPA, Narragansett, RI. (Memorandum

to D.J. Hansen. U.S. EPA, Narragansett, RI.)

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of

heavy metals and cyanide on Mysidopsis bahia (Crustacea: Mysidacea). Aquat.

Toxicol. 7:25-35.

MacDonald, C.R., T.R. Jack and J.E. zajic. 1980. ~tal ion toxicity to

Daphnia magna: A novel approach to data plotting. In: Proceedings of the

sixth annual aquatic toxicity workshop. Klaverkamp, J.F., S.L. Leonhard and

K.E. Marshall (Eds.). Canadian technical report of fisheries and aquatic

sciences No. 975. Department of Fisheries and Oceans, Ot tawa, On tari.o,

Canada. pp. 91-107.

76
~~luegt K.W. t G.S. Schuytema t J.H. Gakstatter and D.F. Krawczyk. 1984.

Toxicity of sediments from three metal-ccnta~inatej are~s. £nviron. Toxicol.

Chem. 3:279-291.

Mann, H. and W.S. Fyfe. 1984. An experimental study of algal uptake of Ut Ba,

V, Co and Ni from dilute solutions. Chem. Geol. 44:385-398.

Aansouri-Aliabadi, t1. and R.E. Sharp. 1985. Passage of selected heavy metals

from Sphaerotil~s (Bacteria: Chlamydobacteriales) to Paramecium caudatum

(Protozoa: Ciliasta). Water aes. 19:697-699.

Markarian, R.K., a.c. Matthews and L.T. Connor. 1980. Toxicity. of nickel,

copper t zinc and aluminum mixtures to the white sucker (Catostomus

commersoni). Bull. Environ. Contam. Toxicol. 25:790-796.

~lartin, J.H. 1979. Bioacc~ulation of heavy netals by littoral and pelagic

marine organisms. EPA-600/3-79-038. National Technical Information Service,

Springfield, VA.

Martin, J.H. and G.A. Knauer. 1972. A comparison of inshore versus offshore

levels of twenty-one trace and major elements in marine plankton. In:

Baseline studies of pollutants in the marine environment (heavy metals,

halogenated hydrocarbons and petroleum). Goldberg, E.O. (Ed.). Brooknaven

National Laboratory. pp. 35-66.

77
Mathis, B.J. and T.F. Cummings. 1973. Selected metals in sediments, water,

and biota in the Illinois River. J. Water Pollute Control. Fed. 45:1573-1583.

Mccabe, L.J., J.M. Symons, R.D. Lee and G.G. Robeck. 1970. Survey of

community water supply systems. J. Am. Water Works Assoc. 62:670-687.

McDermott, D.J., G.V. Alexander, D.R. Young and A.T. Mearns. 1976. Metal

contamination of flatfish around a large submarine outfall. J. Water Pollute

Control Fed. 48:1913-1918.

McFeters, G.A., P.J. Bond, S.B. Olson and Y.T. Tehan. 1983. A comparison of

microbial bioassays for the detection of aquatic toxicants. Water Res.

17:1757-1762.

Mcl~rdy, B.M. and J.J. George. 1985. The uptake of selected heavy metals by

the green alga Cladophora glomerata. Symp. Biol. Hung. 29:2-19.

~1cK1m, J.M. 1977. Evaluation of tests with early life stages of fish for

predicting long-term tOXicity. J. Fish. Res. Board Can. 34:1148-1154.

Mears, H.C. and R. Eisler. 1977. Trace metals in liver from bluefish, tautog

and filefish in relation to body length. Chesapeake Sci. 18:315-318.

Michnowicz, C.J. and T.E. Weaks. 1984. Effects of pH on toxicity of As, Cr,

Cu, Ni and Zn to Selenastrum capricornutum Printz. Hydrobiologia

118: 299-305.

78
:1uramoto, S. 1983. Influence of complexans (tHA, EDTA) on the toxic ity of

nici\.el chloride and sulfate to t: i'sh at high concentrations. v. C:~viro~. Sci.

Health 18A:787-795.

Huramoto, S. and Y. Oki. 1984. Influence of anionic surface-ac tive agents on

the uptake of heavy metals by water hyacinth (Eichhornia crassipes). Bull.

Environ. Contam. Toxicol. 33:444-450.

7:iushak, P. 1980. Metabolism and systemic toxicity of nickel. In: ~hckel in

the environment. ~riagu, J.O. (Ed.). Wiley, New York, ~Y. pp. 499-523.

:·1uska, C. F. 1978. Evaluation of an approach for studying the <Luantitative

response of whole organisms to mixtures of environmental toxicants. Ph.D.

thesis. Oregon State University, Corvallis, OR. Available from: University

l1icrofilms, Ann Arbor, ~n. Order ~~o. 77-29,421.

:·1uska, C.F. and L.J. Weber. 1977a. An approach for studying tne effects of

mixtures of environmental toxicants on whole organism performances. In:

Recent advances in fish toxicology. Tubb, R.A. (Ed.). PB273500 or

EPA-600/3-77-085. National Technical Information Service, Springfield, VA.

:1uska, C.F. and L.J. Weber. 1977b. An approach for stUdying the effects of

mixtures of toxicants. Proc. West. Pharmacol. Soc. 20:427-430.

Nebeker, A.V., C. Savonen, R.J. Baker and J.K. :\.cCrady. 1984. Effects of

copper, nickel, and zinc on the life cycle of the caddisfly Clistoronia

magnifica (Limnephilidae). Environ. Toxicol. Chem. 3:645-649.

79
~ebeker, A.V., C. Savonen and D.G. Stevens. 19ti5. Sensitivity of rainbow

trout early life stages to nickel chloride. Environ. Toxicol. Cbem.

4:233-239.

Neter, J. and W. Ilasserman. 1974. Applied linear statistical models. Irwin,

Inc., Homewood, IL.

Nriagu, J.O. 1980. Cilohal cycle and properties of nickel. In: Nickel in the

environment. Nriagu, J.O. (Ed.). Wiley, New York, ~Y. pp. 1-26.

O'Connor, T.P. 1976. Investigation of heavy ~etal concentrations of sediment

and biota in the vicinity of the Morgantown steam electric gen~rating

station. ~brgantown ~bnitoring Program Report Series.

Ozimek, T. 1985. Heavy metal content in macrophytes from ponds supplied with

post-sewage water. Symp. Biol. Hung. 29:41-50.

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped

bass to organic and inorganic contaminants in fresh and saline waters. Trans.

Am. Fish. Soc. 114:748-753.

Parsons, T.R., C.A. Bowden and W.A. Heath. 1972. Preliminary survey of

mercury and other metals contained in animals from the Fraser River mudflats.

J. Fish. Res. Board Can. 30:1014-1016.

80
Patrick, R., T. Bott and R. Larson. 1975. The role of trace elements in

'marfagetnent of rnIi"sancegth'vths. P13 2!d 98S or EP.~"-660/2-75-008. :la tional

Technical Information Service, Springfield, VA.

Pennington, C.H., J.A. Baker and d.E. Potter. 1982. Contaminant levels in

fishes fron Brown's Lake, Mississippi. J. Miss. Acad. Sci. 27:139-147.

Petrich, S.M. and D.J. Reish. 1979. Effects of aluminum and nickel on

survival and reproduction in polychaetous annelids. Bull. Environ. Contam.

Toxicol. 23:698-702.

Petukhov, S.A. and E.a. ~inonenko. 1982. On the priority of to~icological

"hazard" of nickel in the sea. Har. Pollute BulL 12:426.

Phelps, O.K., 'iJ. Galloway, foP. Thurberg, E. Gould and ~.A. Dawson. 1981.

Comparison of several physiological monitoring techniques as applied to the

blue mussel, ~rytilus edulis, along a gradient of pollutant stress in

Narragansett Bay, Rhode Island. In: Biological monitoring of carine

pollutants. Vernberg, F.J., A. Calabrese, F.P. Thurberg and W.B. Vernberg

(Eds.). Academic Press, New York, NY. pp. 335-35S.

Phillips, G. R. and R. C. Russo. 1978. aetal bioaccumulation in fishes and

aquatic invertebrates: A literature review. EPA-600/3-78-103. National

Technical Information Service, Springfield, VA.

Pickering, Q.H. 1974. Chronic toxicity of nickel to the fathead minnow. J.

Water Pollute Control Fed. 46:760-76S.

81
Pickering, Q.H. and C. Henderson. 1966. The acute toxicity of Some heavy

metals to different species of warmwater fishes. Air Water Pollute Int. J.

10:453-463.

Portmann, J.E. 1968. Progress report on a programme of insecticide analysis

and toxicity-testing in relation to the marine environment. Helgol. Wiss.

Meeresunters. 17:247-256.

Portmann, J.E. 1972. Possible dangers of marine pollution as a result of

mining operations for metal ores. In: Marine pollution and sea life. Ruivo,

M. (Ed.). Fishing News (Books) Ltd., Surrey, England. pp. 343-346.

Pringle, B.R., D.E. Hissong, E.L. Katz and S.T. Mulawka. 1968. Trace metal

accumulation by estuarine molluscs. J. Sanit. Eng. Div. Proc. Am. Soc. Civ.

Eng. 94:455-475.

Pulich, W.M. 1980. Heavy metal accumulation by selected Halodule wrightii

Asch. populations in the Corpus Christi Bay area. Contrib. Har. Sci.

23:89-100.

Rai, L.C. and M. Raizada. 1985. Effect of nickel and silver ions on survival,

growth, carbon fixation and nitrogenase activity in Nostoc muscorum:

Regulation of toxicity by EDTA and calcium. J. Gen. Appl. Microbiol.

31:329-337.

82
Rai, L.C., J.P. Gaur and H.D. Kucar. 1981. Phycology and heavy-metal

pollution. Biol. Rev. Car:::>. Philos. Soc. '56:99-151.

Rehwoldt, R., G. Bida and B. Nerrie. 1971. Acute toxicity of copper, nickel

and zinc ions to some Hudson River fish species. Bull. Environ. Contam.

Toxicol. 6:445-448.

Rehwoldt, R., L.W. !1enapace, B. Nerrie and D. Alessandrello. 1972. The effect

of increased temperature upon the acute toxicity of some heavy metal ions.

Bull. Environ. Contam. Toxicol. 8:91-96.

Rehwoldt, R., L. Lawrence, C. Shaw and E. Wirhowski. 1973. Th~ acute toxicity

of some heavy metal ions toward benthic organisms. Bull. Environ. Contam.

Toxicol. 10:291-294.

Reynolds, B.R. 1979. Trace oetals monitoring at two ocean disposal sites.

EPA-600/3-79-037. ~ational Technical InfonJatian Service, Springfield, VA.

Sata, C., J.L. Schnoor and D.B. McDonald. 1986. Characterization of effects

of copper, cadmium and nickel on the growth of ~litrasomonas europaea.

Environ. Toxicol. Chern. 5:403-416.

Saxena, G.P. and A. Parashari. 1983. Comparative study of the toxicity of six

heavy metals to Channa punctatus. J. Environ. Biol. 4:91-94.

83
See, C.L., A.L. Buikema and J. Cairns. 1974. The effects of selected

toxicants on survival of Dugesia tigrina (Turbellaria). Assoc. Southeastern

Biologists Bull. 21:82.

See, C.L., A.L. Buikema and J. Cairns. 1975. The effects of sublethal

concentrations of zinc and nickel on the photonegative response of Dugesia

tigrina. Va. J. Sci. 26:60.

Seelye, J.G., R.J. Hesselberg and M.J. ~c. 1982. Accumulation by fish of

contaminants released from dredged sediments. Environ. Sci. Technol.

16:459-464.

Shaw, T.L. and v.a. Brown. 1971. Heavy metals and the fertilization of

rainbow trout eggs. Nature 230:251.

Shaw, W.H. and B. Grushkin. 1957. The toxicity of metal ions to aquatic

organisms. Arch. Biochem. Biophys. 67:447-452.

Shcherban, E.P. 1977. Toxicity of some heavy metals for Daphnia magna

Strauss, as a function of temperature. Hydrobiol. J. 13(4) :75-80.

Siraver, M.A. and L.A. Loeb. 1976. Metal activation of DNA synthesis.

Biochem. Biophys. Res. Commun. 7:812-817.

Skaar, H., B. Rystad and A. Jensen. 1974. The uptake of 63Ni by the

diatom Phaeodactylum tricornutum. Physiol. Plant. 32:353-358.

84
Smith-Sonneborn. J •• R.A. Palizzi. E.A. McCann and G.L. Fisher. 1Y83.

B'foas'say of genotoxic e:fects of envitonmect"ll '?ait :cles ic d :eeG:;'''3

ciliate. Environ. Health Perspect. 51:205-210.

Soeder. C.J. and G. Engelmann. 1984. Nickel requirement in Chlorella

emersonii. Arch. Microbiol. 137:85-87.

Solbe. J.F. 1973. The relation between water quality and the status of fish

populations in Willow Brook. Water Treat. Exam. 22:41-58.

Spencer, D.F. and R.W. Greene. 1981. Effects of nickel on seven species of

freshwater algae. Environ. Pollut. (Series A) 25: 241-247.

Spencer. D.F. and L.H. Nichols. 1983. Free nickel ion inhibits growth of two

species of green algae. Environ. Pollute (Series A) 31:97-104.

Sprague. J.B. 1985. Factors that modify toxicity. In: Fundamentals of aquatic

tOXicology - methods and applications. Rand. G.~l. and S.R. Petrocelli (Eds.).

Hemisphere Publishing Corporation. New York. NY. pp. 124-163.

Srivastava. D.K•• S. S. Khanna. V.ti. Srhlast\va and R. Kumar. 1985. Election

diffraction of the metallic elements in the pineal organ of a freshwater

fish. t1ystus vittatus (Bloch). Experimentia 41:603-605.

85
Stephan, C.E., D.I. t~unt, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A.

Brungs. 1985. Guidelines for deriving numerical national water quality

criteria for the protection of aquatic organisms and their uses. PB85-227049.

National Technical Information Service, Springfield, VA.

Stokes, P. 1975. Uptake and accumulation of copper and nickel by metaltolerant strains of Scenedesmus. Int. Ver. Theor. Angew. Limnol. Verh.

19:2128-2137.

Stokes, P.H., T.C. Hutchinson and K. Krauter. 1973. Heavy-metal tolerance in

algae isolated from concaminated lakes near Sudbury, Ontario. Can. J. Bot.

51:2155-2168.

Stokes, P.M., R.C. Bailey and G.R. Groulx. 1985. Effects of acidification on

metal availability to aquatic biota, with special reference to filamentous

algae. Environ. Health Pespect. 63:79-87.

Stratton, G.W. and C.T. Corke. 1979a. The effect of nickel on the growth,

photosynthesis, and nitrogenase activity of Anabaena inaegualis. Can. J.

Microbiol. 25:1094-1099.

Stratton, G.W. and C.T. Corke. 1979b. The effect of mercuric, cadmium, and

nickel ion combinations on a blue-green alga. Chemosphere 10:731-740.

86
Suloway, J.J., W.R. Roy, T.H. Skelly, D.R. Dickerson, R.a. Schuller and R.A.

Griffin. 1983. Chemical and toxicological properties of cC31 fly ash.

Illinois State Geological Survey Division, Champaign, IL.

Swaine, D.J. 1980. Nickel in coal and fly ash. In: Nickel in the environment.

Nriagu, J.O. (Ed.). Wiley, New York, NY. pp. 67-92.

Tarzwell, C.M. and C. Henderson. 1960. Toxicity of less common metals to

fishes. Ind. Wastes 5:12.

Taylor, G.J. and A.A. Crowder. 1983. Uptake and accumulation of copper,

nickel and iron by Typha latifolia grown in solution culture. Can. J. Bot.

61: 1825-1830.

Taylor, G.J. and A.A. Crowder. 1984. Copper and nickel tolerance in Typha

latifolia clones from contaminated and uncontaninated environments. Can. J.

Bot. 62:1304-1308.

Thompson, S.E., C.A. Burton, D.J. Quinn and Y.C. ~~g. 1972.- Concentration

factors of chemical elements in edible aquatic organisms. UCRL-50564. Rev. 1.

National Technical Information Service, Springfield, VA.

Timourian, H. and G. Watchmaker. 1972. Nickel uptake by sea urchin embryos

and their subsequent development. J. Exp. Zool. 182:379-388.

87
Timourian, N. and G. Watchmaker. 1977. Assay of sperm motility to study the

effects of metal ions. In: Biological implications of metals in the

environment. ERDA Symposium Series 42.

Tong, 5.5., \~.D. Youngs, W.H. Gotenmann and D.J. Lisk. 1974. Trace metals in

Lake Cayuga lake trout (Salvelinus namaycush) in relation to age. J. Fish.

Res. Board Can. 31:238-239.

Trollope, D.R. and B. Evans. 1976. Concentrations of copper, iron, lead,

nickel and zinc in freshwater algal blooms. Environ. Pollute 11:109-116.

u.s. EPA. 1975. Preliminary investigation of effects on the environment of

boron, indium, nickel, selenium, tin, vanadium and their compounds.

EPA-560/2-75-005C. National Technical Information Service, Springfield, VA.

u.s. EPA. 1976. Quality criteria for water. EPA-440/9-76-023. National

Technical Information SerVice, Springfield, VA.

u.s. EPA. 1980. Ambient water quality criteria for nickel~ EPA-440/S-80-060.

National Technical Information Service, Springfield, VA.

u.s. EPA. 1983a. Methods for chemical analysis of water and wastes.

EPA-600/4-79-020 (Revised March 1983). National Technical Information

Service, Springfield, VA.

88
U.S. gPA. 1983b. Water quality standards regulation. Fed. Regist.

48: 51400-51413. November 8.

U.S. EPA. 1983c. Water quality standards handbook. Office of Water

Regulations and Standards, Washington, DC.

U.S. EPA. 1985a. Appendix B - Response to public comments on "Guidelines for

deriving numerical national water quality criteria for the protection of

aquatic organisms and their uses." Fed. Regist. 50: 30793-30796. July 29.

U.S. EPA. 1985b. Technical support document for water-quality based taxics

control. Office of Water, Washington, DC. September.

U.S. EPA. 1986. Chapter 1 - Stream design flow for steady-state modeling. In:

Book VI - Design conditions. In: Technical guidance manual for perfot'llling

waste load allocations. Office of Water, Washington, DC.

Uthe, J.F. and E.G. ~ligh. 1971. Preliminary survey of heavy metal

contamination of Canadian freshwater fish. J. Fish. Res. Board Can.

28:786-788.

Van Coillie, R. and A. Rousseau. 1974. Mineral composition ~n scales of

Catostromus commersoni exposed to different media: Analysis by micro-electron

technique. J. Fish. Res. ~ard Can. 31:63-66.

89
Van Hoof, F. and J.P. Nauwelaers. 1984. Distribution of nickel in the roach

(Rutilus rutilus L.) after exposure to lethal and sublethal concentrations.

Chemosphere 13:1053-1058.

Verma, S.R., M. Jain and R.C. Dalela. 1981. In vivo removal of a few heavy

metals in certain tissues of the fish Notopterus notopterus. Environ. Res.

26:328-334.

Vymazal, J. 1984. Short-term uptake of heavy metals by periphyton algae.

Hydrobiologia 119:171-179.

Wachs, V.B. 1982. Concentration of heavy metals in fishes from the river

Danube. Z. Wasser Abwasser Forsch 15:43-49.

Wang, H.K. and J.M. \Jood. 1984. Bioaccumulation of nickel by algae. Environ.

Sci. Technol. 18:106-109.

Wang, W. 1986. Toxicity tests of aquatic pollutants by using common duckweed.

Environ. Pollute (Series B) 11:1-14.

Wang, Z., C.P. Bianchi and S.R. Narayan. 1984. Nickel inhibition of calcium

release from subsarcolemnal calcium stores of molluscan smooth muscle. J.

Pharmacol. Exp. Ther. 229:696-701.

Warnick, S.L. and H.L. Bell. 1969. The acute toxicity of some heavy metals to

different species of aquatic insects. J. Water Pollute Control Fed.

41:280-284.

90
Waterman, A.J. 1937. Effect of salts of heavy metals on the development of

the'li;rea u'tchin, At''Sac1 2 punctulata. Bioi. 311] 1. (Woods' 'Hole) 1'3: 401'~420.

Watling, H.R. 1983. Comparative study of the effects of metals on the

settlement of Crassostrea gigas. Bull. Environ. Contam. Toxicol. 31:344-351.

Watras, C.J., J. MacFarlane and F.M. Morel. 1985. Nickel accumulation by

Scenedesmus and Daphnia: Food-chain transport and geochemical implications.

Can. J. Fish. Aquat. ScL 42:724-730.

Weber, W.J., Jr. and W. Stumm. 1963. Mechanisms of hydrogen ion buffering in

natural waters. J. Am. Water Works Assoc. 55: 1553-1578.

Wehr, J.D. and B.A. ~fuitton. 1983. Accumulation of heavy metals by aquatic

mosses. 2: Rhynchostegium riparioides. Hydrobiologia 100:261-284.

Weinstein, N.L. and P.O. Anderson. 1978. Lethal and sublethal toxicities of

copper-nickel mixtures to the zebrafish Brachydanio rerio. In: Proceedings of

the fourth annual aquatic toxicity workshop. Davis, J.D., -G.L. Greer and 10K.

Birtwell (Eds.). Fisheries and Marine Service Technical Report No. 818.

Department of Fisheries and Oceans, Ottawa, Ontario, Canada. p. 154.

Whitley, L.S. and R.A. Sikora. 1970. The effect of three Common pollutants on

the respiration rate of tubificid worms. J. Water Pollute Control Fed.

42:R57-R66.

91
Whitton, B.A. and F.H.A. Shehata. 1982. Influence of cobalt, nickel, copper

and cadmium on the blue-green alga Anacystis nidulans. Environ. Pollute

(Series A) 27:275-281.

Willford, W.A. 1966. Toxicity of 22 therapeutic compounds to six fishes.

Investigations in Fish Control 18. u.s. Fish and Wildlife Service,

Washington, DC.

Wilson, J.G. 1983. The uptake and accumulation of Ni by Cerastoderma edule

and its effect on mortality, body condition and respiration rate. Mar.

Environ. Res. 8:129-148.

Wilson, W.B. and L.R. Freeberg. 1980. Toxicity of metals to maFine

phytoplankton cultures. EPA-600/3-80-02S. National Technical Information

Service, Springfield, VA.

Windom, H.L., K. Tenore and D.L. Rice. 1982. Metal accumulation of the

polychaete Capitella capitata: Influences of metal content and nutritional

quality of detritus. Can. J. Fish. Aquat. Sci. 39:191-196.

WOng, P.T., Y.K. Chau and P.L. Luxon. 1978. Toxicity of a mixture of metals

on freshwater algae. J. Fish. Res. Board Can. 35:479-481.

WOng, P.T.S., Y.K. Chau and D. Patel. 1982. Physiological and biochemical

responses of several freshwater algae to a mixture of metals. Chemosphere

11:367-376.

92
Wong, S.L. and J.L. Beaver. 1980. Algal bioassays to determine toxicity of

metals mixtures. Hydrobiologia 74:199-208.

Wren, C.D., H.R. Maccr~on and B.R. Loescher. 1983. Examination of

bioaccumulation and biomagnification of metals in a precambrian shield lake.

Water Air Soil Pollute 19:277-291.

Yan, N.D., G.E. Miller, I. Wile and G.G. Hitchin. 1985. Richness of aquatic

macrophyte floras of soft water lakes of differing pH and trace metal content

in Ontario, Canada. Aquat. Bot. 23:27-40.

Young, D.R. 1982. A comparative study of trace metal contamination of the

Southern California and New York Bights. In: Ecological stres~ and the New

York Bight: Science and management. Mayer, G.F. (Ed.). Estuarine Research

Federation, Columbia, SC. pp. 249-262.

Zaroogian, G. E. and }t. Johnson. 1984. Nickel uptake and loss in the bivalves

Crassostrea virginica and Mytilus edulis. Arch. Environ. Con tam. Toxicol.

13: 411-418.

Zaroogian, G.E., J.H. Gentile, J.F. Heltsche, U. Johnson and A.M. Ivanovici.

1982. Application of adenine nucleotide measurements for the evaluation of

stress in Mytilus edulis and Crassostrea virginica. Comp. Biochem. Pnysiol.

7IB: 643-649.

93
U.S. tn\llrOrIl1\~lItdl p!(,i:,c:1: ;, IIt'vi'l:'\'

Rc~ion 5, Library (i- L - L~ J)

77 West Jackson BOl!j\~" ::r1j, 1.:(0 i-, :,;:

Chicago, IL 60C04-3590