UnitedStates EnvlronmeAtalProtection Agency OfficeofWater RegulationsandStandards CmerlaandStandardsDivISion WashingtonDC 20460 EPA**440/5-86~04** September1986 

# &EPA



# .. Water 

# Ambient WaterQuality Criteria for Nickel-1986

a

### AMBIENT AQUATIC LIFE WATERQUALITY CRITERIA FOR NICKEL

U.S. ENVIRONMENTAL PROTECTION AGENCY

OFFICE OF RESEARCHAND DEVELOPMENT ENVIRONMENTAL RESEARCH LABORATORIES DULUTH, MINNESOTA NARRAGANSETT, RHODE ISLAND

### NOTICES
This document has been reviewed by the Criteria and Standards Division, Office ofWater**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 publishwater quality criteria that accurately reflect the latest scientific knowledge on the kind and extent of all identifiable effects onhealth and welfare that might be expected from the presence of pollutants in any body ofwater, including ground water. This document is a revision ofproposed criteriabased 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 CleanWater Act, section 304(a)(1) and section 303(c)(2). The termhas 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. Ifwater quality criteria associated with specific streamuses 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 criteriabecome 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.

WilliamA. Whittington Director

- Office ofWater Regulations and Standards

### ACKNOWLEDGMENTS

Loren J. Larson JudyL. Crane (freshwater authors) University ofWisconsin-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

v1. 

### 2. 3.

4. 5. 

### 6. TABLES
Acute Toxicity ofNickel 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 ofNickel 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 1nmost 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 ofeffluent 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 ofmost samples of ambient water probably will not affect the result substantially. 8. The carbonate systemhas amuch 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.

310. 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. 

### 4Acute 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 ofas 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 of4.8. 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 Daphniamagna, 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). Asimilar 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 ofyoung 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 ofhardness 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.



### 9Division 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 ofhardness 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.

10Brown 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. Asimilar 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. Afield 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.
12Willford (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 ofheavy 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, 13nickel 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, Arbacia**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 Scoopa 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-Avila 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 ofGerhards 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
16invertebrates 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 Daphniamagna 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
17and 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 18spec1es of some metals cannot be measured because the total**r~cvverable** method cannot distinguish between individual oxidation states, and (2) 1n
some cases these criteriamight 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).

19Table I. AcuteToxicity ofNickel toAquatic Animals Hardness LC50 Adjusted SpeciesMean (mglL as or EC50 LC50 orEC50 AcuteValue Species Method· Chemical**caCO~** (Ilg/U" (Ilg/U"· (Ilg/U
..•• Reference FI<ESHWATER SPECIES Worm, S, M 50 14,100 14,100 14,100 Rehwoldt at dl. 1'J75 Nals SP. Snail (embryo), S, M 50 11,400 11,400 RehwoIdt 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 Cladocerdn, S, U Nickel 45.3 510 554.4 BIesInger and paphnIa_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 Nickel 100 2,360 1,313 Cladoceran, S, M Chapman et al• Q.aphnia maqna Chloride Manuscript Cladoceriln, S,**,~** Nickel 104 1,920 1,033 Chapman et al• DaphnIa_magna Chloride ManuscrIpt 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 LInd at al• Daphnia**pul~~drla** sulfate Manuscript CIildoceran, 5, M Nickel 48 \,813 1,877 LInd et al.**DaDhn..l~ ~Llcari**  a suitate Manuscript Cladocaran, 5, M Nickel 44 11,836 2,046 Lind at al. Daphnia pulicarla suIfate ManuscriptTlible 1. (Continued) Hardness LC50 Adjusted SpeciesMelIn (mglL as orEC50 LC50 orEC50 AcuteValue 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 pulIcarla sulfate Manuscript Amphlpod, 5, M 50 13,000 n,ooo 13,000 Rahwoldt at al. 1973 Gammarus sp. Mayfly, 5, U NIckel 42 4,000 4,636 4,636 WarnIck and Bell iE.hemerella subvarla suIfate 1969 Damselfly, 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 BelI Acroneurla**Iycor~** sulfate \969



### ------ Caddlsfly, 5, M 50 30,200 30,200 30,200 Rehwoldt et al. UnldentIfied sp. 1973 American eol, 5, M Nickel 53 n,ooot 12,370 Rehwoldt at al.**~~** rostrata nitrate \971 N AmerIcan 8eI , 5, M 55 13,000 11,990 12,180 Rehwoldt et al. r-**~~** rostrata 1972 Ralnbow trout (2 mos), F, M Nickel**~5,500** Hale \977 Salmo galrdnerl nitrate Rainbow trout (juvenile), F,**~~** Nickel 20,lOOt Anderson 1981 2.-a1mo2irdneri sulfdte Rainbow trout (juvenile), F, M Nickel 12,700t Anderson 19tH Salmo qalrdneri sulfate Rainbow trout (juvenile), F, M Nickel 28,000t Anderson 1981**~~** qaIrdneri 5U

### qdte Rainbow trout (juvenile), F, M Nickel**~0,900t** Anderson 1981 Salmo galrdneri sulfate RaInbow trout (juvenile), F, M Nickel 16,900t Anderson 19tH Salmo galrdnerl suifateTlIble 1. C contInued) Hardness LC50 Adjusted SpeciesMean CmglL as orEC50 LC50 or EC50 AcuteValue Species Method· Chemical Cllg/U" C\lg/U·" Ceg/U.... Reference Rainbow trout (juvenlIe), f, M Nlckal 15,900t Anderson 1981 Salmaqairdnerl 5ulti'lte Halnbow trout (.juvenile), f, M Nlckal 11•**~OO** t Anderson 1981 Salmoqairdneri 5ultate Rainbow trout (juvenlIe). f, M "llckel 11,I00t Anderson 1981 Salmo galrdnerl suItate 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~** **~!!dner** i chlorl<1e**~9** Rainbow trout (12 mos), F. M Nickel 27- H.900 12.6')0 Nebeker et al. 1985 Salmo galrdnerl chiorIde**~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 chlorIde Henderson 1966 IV Common carp «20 em), S, M Nickel**5~** 10,600t 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 chloride Henderson 196b Fathead minnow (1-2 g), S, 1I Nickel 20 4.580 9,943 PickerIng and**~Imephales** promelas chloride Henderson 1966 Fathead minnow (1-2 g), S. U NickeI**~60** 42,400 7,981 Pickering and £,Imephales**prome~** chloride Henderson 1960 Fathei'ld minnow (1-2 g). S, U "llckeI 360 44,500 8,376 Pickering and Plmephales promelas chloride Henderson 196bTableI. (continued) Hardness LC50 Adjusted Specles Mean (mglL as orEC50 LC50 orEC50 AcuteValue 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 PickerIng 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 LInd at al. PImephaIes**.£!"~~** sulfate Manuscript Fathead minnow, F, M Nickel 44 5,163 5,753 8,027 LInd at ale Plmephales_promelas sulfate Manuscript Banded killifish «20 em), 5, M Nickel**5~** 46,200t 43,980 Rehwoldt et al• fundulus dlaphanus nitrate 1971

N Banded killIfish, 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 13,600t 12,950 RehwoIdt at al.**~~** americana nitrate 1971 WhIte perch, 5, M 55 13,700 12,640 12,790 RehwoId1 ut al. Morone americana 11)72 StrIped b<lsS (flnqerlInq), S, M Nickel 53 6,200t 5,902 Rehwoldt at al. Morone saxatilis nitrate 1971 Striped bass, 5, M 55 6,300 5,B12 RehwoIdt et al. Morone saxatiIis 1972



### ---- Striped bass (63 day), 5, lJ Nickel 40 3,900 4,710 Palawskl et al. 1985 Morone si1xatI IIs chloride



### --------Table 1. (continued) Hardness lC50 Adjusted SpecIes Mean (mg/l as or EC50 LC50 or EC50 Acute Value Species Method· Chemical (lIg/U" (1I9/U"· (!!g/U·

..• Reterence StrIpad bass (63 day), 5, U Nickel 285 33,000 7,569 5,914 Palawskl et al. 19t:b Marone saxatl I15 chloride



### ------ Rock bass, F, M f-lickel 26 2,480 4,312 4,312 Lind at al. Ambloplites rupestr15 suIfate ManuscrIpt PumpkI nseed «20 cm), 5, M Nickel 53 8,lOot 7,710 Rehwoldt at al• Lepomls**qlb~** nitrate 1971 PumpkInseed, 5, M 55 8,000 7,380 7,544 Rahwoldt et al. Lepomls**_9.~osus** 1972 BI USC]III (1-2 q), 5, U Nickel 20 5,180 11,250 Plckarlnq and Lepom15_macrochIrus chlorIde Henderson 1966 A Iueqlll (1-2 q), 5, U Nickel 20 5,360 11,640 Pickering and Lepomls macrochirus chloride Henderson 1966 IiIusqI I I (1- 2 q), 5, U Nickel 360 39,600 7,454 Plckerlnq and Lepomls macrochirus chloride Henderson 1966 N .j:'- BluegIII, F, M Nickel 49 21,200 21,570 12,040 Cairns et al. 19tH Lapomls macrochlrus chlorideTabIe 1. (continued) LC50 SpeciesMelin Salinity orEC50 AcuteValue Species Method- Chemical (g/kg) (pg/U" (lJglU Reference SALTWArER SPECIES Polychaete OIorm (adult), S, U 

### tnckel 49,000 49,000 PetrIch andReish 1979**I~erols** arenaceodentata chloride Polychaete OIorm (adult), S, U**I~ickel** 20 L5,OOQ 25,000 Eisler andHennekey 1977 Nereis vlrens' chloride Polychaete worm (adult), S, U Nickel 17,000 17,000 Petrich andReish 1979 CtenodrlIus serratus chlorIde Polychaete OIorm (adult), S, U Nicktd >50,000 >50,000 Petrich and Reish 1979 Capltelld capitata chlorIde Mud soa;I (adult), S, U NIckeI 20 72,000 72,000 Eisler and Hennekey 1977 NassarIus obsoletus chlorIde Eastern oyster (embryo), S, U**I~I**ckel 75 1,180 1,180 Calabrese 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 Mdcomabalthica chlorIdu <lO°C) Clam, S, U Nickel 25 560,000 Bryantet al. 19t15 Macomd balthicd chloride (10°C) Clam, S, U Nickel 35 1,100,000 Bryant et al. 1<)t.l5 Macoma balthica chlorid", (J0°C) CldlO, S, U Nickl;\ 15 110,000 Bryant at al. 1985 Macoma balthlca chlo,.IJe (J5°C)Table 1. (continued) LC50 SpeciesMean Salinity orEC50 AcuteValue Species Method* Chemical (g1kg) (pg/Un (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 Macomabdlthlca chloride (15°C) Quahog clam (&nbryo), S, U Nickel 25 310 310 Calabrese andNelson Mercendrlamercenarla chloride 1974 Soft-shell clam (adult), S, U Nickel 20 320,000 Eisler andHennekey 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 andCardIn 1985 Eurytemora afflnis chloride Copepod (adult), 5, U Nlck",1 30 '),593 11,240 Lussier andCardin 1985 Eurytemora affinis chloride Copepod (adult), S, U NiCkel 30 3,466 3,466 Lussier andCardin I'Jd5 Acartid**c1au~** I chloride N 0\ Copepod (aduIt), 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 (juIJenlie), 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 chlorIde (5°C) Amphipod, 5, U NIC'kel 10 21,000 Bryant et al. 1985 Corophlum IJolutator chloride (5°C)Table 1. (continued) LC50 SpeciesMean Salinity orEC50 AcuteValue Species Method* Chemical (g/kg) (pg/U** (lJg/U Reference Amphipod. S. U Nickel 15 18.000 Bryant at al. 1985 Corophtum volutator Chloride (5°C) Amphlpod. S. U N IckeI 25 36,000 l3ryant at al. 1985 Coraphtum volutator chlorI<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 Bryantat al. 1985 Corophium volutator chloride <10°C) AlnphIpod. S. U N Iekel 2? 24.000 Bryant at al. 1985 Curophlumvolutator chloride <1O°C) Amphipod. S. U Nickel 35 52.000 Bryantat al. 1985 Corophlum volutator chloride (10 0e) N ---.J Nickel al. 1985 Amphlpod. S. U 5 5.600 Bryant at 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 chlorideTable 1. (continued)
Species Method· Chemical Starfish (adult), S, U Nickel Asterlas forbesll chlorIde MummIchog (adult), S, U Nickel Fundulus heteroclltus chlorIde Mummlchog (adult), S, U NIckel Fundulus heteroclltus chlorIde MummIchoq (adult) , 5, U Nickel Fundulus heteroclltus chlorIde Atlantic sllllerside S, U Nickel (Iarlla), chlorIde Menldla menldla TIdewater slillersIde S, U NIckel (jullenIIe), chiorIde Menldla penlnsulae
N StrIped bass (63 day), 5, U Nickel 00 Morone saxatll Is chlorIde Spot (jullenlle), 5, U Nickel Lelostomus xanthurus chlorIde SalinIty (g/kg)

20

6.9
21.6
20
30

20

21 lC50 SpecIes 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 Isler and Hennekey 1977

7,958 7,958 CardIn 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 Specles M3an Acute Values are calcuiated at hardness

### =50 mg/L (as CaCD3). In rIller water.N \.0 Table 1. (continued)

Results ofCovarianceAnalysis ofFreshwaterAcuteToxicity versus Hardness Species n Slope 95_ConfidenceLimits Degrees ofFreedom Daphnlamagna 6 1.1810 0.3187, 2.0433 4 Fathead mlnnow 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

ItP 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. Daphnla magna chloride 21.4 ManuscrIpt Cladoceran, LC Nickel 105 101- 123.1 Chapmi!ll at al• Daphnla magna chloride 150 Manuscript CIadoceran, LC Nickel 205 220- }56.6 Chapmi!ll at al. Daphnla magna chloride 578 "'anuscrIpt CI**~doceran** (1st generation), LC Nickel 5-10 7.071 Lazareva 1985 Daphnia magna suifate CIadoceran (2nd generation), LC Nickel <5**- <5 Lazareva 1965 Daphnia magna sulfate Cladoceran Ord generation)• LC Nickel 5-10 7.071 lazareva 1965 Daphnla magna**~ulfate** CIadoceran (4th generation), lC Nickel 5-10 7.071 lazareva 1965 w DaphnI a magna sulfate 0 Caddlstl", LC Nickel 54 66- 126.4 Nebeker at al. 1984 CIIstoronla magnifica chloride 250 RaInbow trout, ElS Nickel 5} <35"- <35 Nebeker et**~I** • 1985 galrdnerl chlorIde RaInbow trout, ElS Nickel 52 62- 91.15 Nebeker et al. 1985 galrdnerl chlorIde 134 RaInbow trout, ELS Nickel 49 134- 240.3 Nebeker et al• 1985 galrdnerl chlorIde 431 Fathead minnow, LC Nickel 210 360- 526.7 PickerIng 1974 Plmephales promelas chlorIde 730 Fathead minnow, ElS Nickel 44- 108.9- 217.3 Lind etal. Plmephales promelas suifate 45t 433.5 Manuscript**----~------~---**Tabl. 2. (CoAtlnued) Specl.S Salinity (g/kg) U.lts (pgA)•• a.ronicVal
.. 

### "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 :: early lite-stage• 

## •• Results are based on measured concentrations of nickel. AAA Unacceptable effects occurred at all concentrations tested. t \lalues from a:;ute tests In Table 1.



### o 2 

### Spec••s n Slope 95'Conf.dencel,.,ts 

### oaphnIa 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.sultsofRegreSSionAnalysisofFr.shwaterChronicToxicityversusHardness Degr

..sofFreedew

......

• Cannot be calcuiated because degrees of freedan '" O.


### ** P '" 0.19 for equality of slopes wltn 1 degree of freedan.W N Table2. (Continued) Aeute-ChronleRatio HardneS5 (119ft

### es AcuteValue ChronIeValue Species Caco,) (lIg/U (eS/U 

### .!!!.!.!2. Cladoceran, 51 1,800 14.17 122.4 DaphnIamagna Cladoceran, 104- 1,920 123.1 15.60 DaphnIamagna 105 Cladoceran, 205- 4,970 356.6 13.94 Daphnlamagna 206 fathead mInnow, 210 27,930· 526.7 53.03 Plmephales promelas fathead minnow, 44- 5,186l1l1 217.3 23.87 Plmephales promelas 45 Mysld, 30.ltlt 508 W-.74 5.418 Mysldopsls bahla

• Geometricmean of four values InTable 1.
1111 GeometrIc medn of two values InTable I.
All. SalInity (g/kg).Table }. RankedGenusMaanAcuteValueswIthSpecIesMeanAcute-ChronlcRatIos GenusMean Specl_Mean Specl_Mean AcuteValue AcuteValue 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 GoldtIsh, 21,320 Carasslus auratus 14 21,200 DMlselfly, 21,200 UnIdentlfled sp. 13 14,100 Worm, 14,100 sp. w 12 13,380 RaInbow trout, 13,380 w Salma galrdnerl 11 13,000 AmphIpod, 13,000 Gammarus sp. 10 12,770 Sna\I, 12,770 Amnlcola sp. 9 12,180 Amerlean eel, 12,180 AnguIlla rostrata 8 9,839 Common carp, 9,839 Cyprlnus carpIo 7 9,661 Guppy, 9,661 Poecliiaretlculata

# . 6 8,697 Wh1te perch, 12,**7~** Morone americana Strlpad bass, 5,914 Morone saxatlilsTeble1. (ContInued) Genus ....n SpecIesMNn SpecIes....n AcuteValue AcuteValue Acute-Chronlc (pS/U" SpecIes (ps/U"· RatIo···· 5 9,530 Pumpkinseed, 7,544 Lepomls glbbosus BIuegIII, 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 CIadoceran, 2,042 Daphnia pullcarla C Iadoceran, 1,102 29.86tt Daphnlamagna w po SALTWATER SPECIES 20 320,000 Soft-shell clam, 320,000 arenarla 19 294,500 Clam, 294,500 Macoma balthlca 18 150,000 StarfIsh, 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**-----~--~** -----Table3. (ContInued) GenusMe8n SpecIesMeen Specl_
...... AcuteValue AcuteValue Acute-e
....onlc (pS/U" SpecIes (.g/U"· R.tlo···· 14 >50,000 Polychaete worm, >50,000 CapItellacapltata 13 47,000 HermItcrab, 47,000 Pagurus longlcarpus 12**~5,OOO** Polychaete worm, 49,000 Nerets arenaceodentata PoIychaete worm, 25,000 Nerels vIreos 11 21,000 StrIped bass, 21,000 Morone saxatliis 10**17,~90** AtlantIc sllverslde, 7,958 Menldlamenldla Tidewater sllverslde, 38,000 w Menldlapenlnsulae U1 9 17,000 PoIychaete worm, 17,000 Ctenodrllus serratus 8 18,950 Amphlpod, 18,950 Corophlumvolutator 7 11,240 Copepod, 11,240 Eurytemoraafflnls 6 6,000 Copepod, 6,000 Nltocra splnlpes 5**~,466** Copepod, 3,466 Acartlaclausl 4 1,180 Eastern oyster, 1,180 CrassostreavIrgInleaTable }. (Continued) Genus
....n SpeciesMean Species ...... AcuteValue AcuteV.lue Acute-Chronlc ("g/U" Species (

..g/U

.... R.tlo···· 3 567.5 Mysld, 508 5.478 Mysldopsls bahla MysId, 634 Mysldopsls blgelowl 2 310 Quahog clam, 310 Mercenarlamercenarla 15\.7 Mysld, 151.7 Heteromysls formosa

- Ranked fran most resistant tomost sensItive based on Genus Mean Acute Value. Inclusionof "greater than" values does not necessarIly Imply a "true ranking, butdoes allow use of all genera for whIch data are available so that the Final AcuteValue Is not unnecessarily lowered.



# -- Freshwater Genus Mean Acute Values are at hardness

### =50mg/l. w Q'\



# --- FromTable 1; freshwater v81ues are at hardness

### =50 mg/l.



# ---- FromTable 2. t Geometric mean of two values In Table 2. tt GeometrIc 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

### =50mg/U Pooled Slope

### =0.8460 (see Table 1) In<789.0) - Islope x In(50)1 6.6708 - (0.8460 x 3.9120) = 3.3612 CrIterIon MaxImum Concentration = e(0.84601In(hardness)H3.3612) Final Acute-Chronic Ratio

### = 17.99 (see text) Final ChronIc VaIue

### = (l,578 Ilg!U I 17.99

### =87.72 Ilg/L (at hardness

### =50 mg!U Assumed ChronIc 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 Valus

### = 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/LTable4. TOKlcity of Nickel to Aquatic Plants
Hardne•• (Illg/L •• Duration eoncentr.tl

.. Species Ch_lcal**~)** (day.) Effect hg/U· Reference FRESHWATER SPECIES BIue-green alga, NIckel 14 84% reductIon 600 Spencer and Greene Anabaena flos-aquae nItrate In gro.rth 1981 BIue-green alga, NIckel 8 IncIpIent 5 BrIngmann and Kuhn**Mleroe~stls** aeruglnosa chloride Inh10ItIon 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% reductIon 100 Spencer and Greene Anklstrodesmus falcatus nItrllte In growth 1981 Green alga, NIckel 14 42% reductIon 100 Spencer and Greene Anklstrodesmus falcatus nItrate In growth 1981 I/ar. aclcularJs Green alga, NIckel nitrate or 41.5 12 91%reductIon 100" Hutchinson 19H; LV Chlamydomonas eugametos "lIekel suIfate 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 HutchInson 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% reductIon 300" HutChinson 1973; Haematococcus capensls NIckel suifate In qro.rth ItJtchInson 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** HutchInson 19H; Scenedesmus acumlnata NIckel suifate In growth Hutchinson and Stokes 1915rable 4. (Continued)

Species Green alga, Scenedesmus acumlnata Ch8lllical Nickel nitrate or

NlckeI suifate Hardne.s (Mg/L as**C~)**

47.5 Duration (days) Effect 13 Reduced growth CoRcentratIon (ps/L)- Reference

500 Stokes et al. 1973; HutchInson 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 chiorIde

NIckel chlorIde

Nickel nltrate Nickel nitrate Nickel chloride

Nickel chloride 14.96 14
10
8

14
14
28

4
28**30~** reduction In**qro~h** 47% reduction In groltth Incipient Inhlbltlon**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 DevI Prasad and Devl Prasad 1982 BrIngmann and Kuhn 1977a; 1978a,b; 1979; 1980b Spencer and Gieene 1981 Fazy et al. 1979
Brown and Rattigan 1979 Wang 1986
Brown and RattIgan 1979 Water hyacInth, Elchhornla crasslpes water hyacInth, Elchhornla crasslpes Nickel chiorlde

Nickel chloride 12
12 38
38**30~ r~uctlon**  4,000 In growth 29% rbductlon 8,000 In**qro~h** Muramoro and OkI 1984 Muramoto and OkI 1964

Giant kelp (young fronds), Macrocystls pyrlfera SALTWATER SPECIES 4 EC50 (reduc- 2,000 tlon In photosynthesIs) ClendennIng and North 1959

• Results are expressed as niCkel, not as the chemical.Table 5. Bloac;cUlllulaton of Nickel by AquatIcOrganI$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 hyacInth. 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 chlorIde tops 500.3 Water hyacInth. NIckel 8,000 38 12 Root 335.5 Muramoto and Okl 1984 Elchhornla crasslpes chlorIde tops 576.2 CIadoceran, 63NI In Whole 100 Hall 1978 Daphnia magna O.IM HCI body CIadoceran, 50 20.1 3.75 Whole 192·" Hall 1982 Daphnia magna body
.p- CIadoceran• 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 Daphnla magna chlorIde body RaInbow trout, Nickel 1.000 320 180 Muscle 0.8 CalamarI 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• Iotinuscrtpt Plmephales promelas suifate body Fathead mInnow. NIckel 108.9 30 Whole 47 LInd et al. Manuscript Plmephales promelas sulfate body
SALTWATER SPECIES Rockweed• 1.2 Field Whole 675t foster 1976 Fucus veslculosls collections plantTable5. (Continued) Hardness ConceAtratIon (.-gIL as Duration Species Ch.lcal In Water (,g/U-**C~)** (days) Tissue BCForBAF" Reference Brown macroalga, 1.2 FIeld \JtloIe 458.3t Foster \976 Ascophyllumnodosum collections plant BIue mussel, NIckel 4.4 84 Soft 4n.7 Zarooglan and Johnson Mytllus edulls suifate parts 1984 81ue mussel, NIckel 10.0 84 Soft 328.6 Zaroogl"n and Johnson MytIIus eduIIs suifate parts 1984 Eastern oyster, NIckel 4.2 84 Soft 458.1 ZaroogIan and Johnson Crassostrea vlrglnlca suifate parts 1984 Eastern oyster, NIckel 9.9 84 Soft 261.8 ZaroogIan and Johnson Crassostrea vlrglnlca suifate parts 1984



## * Measured concentratIon of nIckel.

1I1l Bloconcentratlon factors (BCFs) and bloaccumulatlon factors (BAFs) are based onmeasured concentratIons of nIckel In water and In tissue.
Ull Estlmate1 fran graph. t Factor was converted from dry weIght to wet weight basIs.Table6. OtherootaonEffectfiofNlcke. onAquaticOrga.ls-a Speclefi Hardne•• (lIl9Il

# a. CoCO) Duration fRESHWATER SPECIESEft.ct ConcentretIon (,s/l)· Reference
Alga, Chlorella pyrenoldosa Green alga, Scenedesmus quadrlcauda
Green alga. Scenedesmus quadrlcauda Nickel chlorIde

NIckel ammonIum

suifate 24 hr
96 hr

96hr Reduced growth IncIpIent InhIbltIon (rIver water) IncIplent InhibitIon (rIver water) 88 1,500

900 Gerhllrds lind WeiIer 1977 BrIngmann and Kuhn 1959a,b Brlngmann and Kuhn 1959a,b Alga, (mh<e:I popuIatIon)
Blue-green alga, Anabaena cyllndrlca
BIue-green alga, Anabaena cyllndrlca NIckel nItrate

NIckel suifate
NIckel suifate 87- 99 <53 days

5 days

5 days Decrease In dIatom dIversity; sh1ft to green and blue-green algae tb effect on doubling tIme (In lIght> 13% re:luctlon In dOublIng tIme (In dark) 2- 8.6

15.I

15.1 PatrIck at al. 1975

Daday et al. 1985
Daday et al. 1985

BIue-green alga, Anabaena cyllndrlca BIue-green alga, Anabaena cyllndrlca BIue-green IIIga, Nostoc Iinckla Blue-green alga, Nostoc IInckla BIue-green alga, Nostoc muscorum BacterIlI1I, 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 (nItrate reductIon) EC50 (ammonla uptake) EC50 (survIVllI) Reduction In abundance 1,885 1,14I

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 1983Tabl.6. (contInued) Hardn.ss (IIQI'Las CoItcentratlon Specl.s Ch_Ical CeOO,s) DuratIon Effect 

### ("slL)- R.f
......c. BacterIlJIl. Nickel 40 24 hr** Reduction In 5 Babich and Stotzky BacIIIus brevIs chiorIde abundance 1983 Bacterium. Nickel 40 24 hrtt* ReductIon In 5 Babich and Stotzky BacIIIus cereus chloride abundance 1983 Bacterium. Nickel Incipient 100 BrIngmann and Kuhn EscherIchla coil chloride InhlbItlon 1959a BacterIum. Nickel Incipient 100 Brlngmann and Kuhn EscherIchIa coil ammonIum Inhibition 1959a suItate Bacterlum. NIckel 16 hr Incipient 2.5 BrIngmann and Kuhn Pseudomonas e.utlda chlorIde InhIbltIon 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 bacterla chlorIde (survival) Protozoan. Nickel 72 hr Incipient 140 BrIngmann 1978; Entoslphon sulcatum chloride Inhibition Brlngmann and Kuhn 1979; 1980b; 1981 Protozoan. Nickel 28 hr Incipient 50 Brlngmann and Kuhn Mlcroregma heterostoma chloride Inhibition 1959b Protozoan. Nickel 28 hr IncI plent 70 BrIn!J1lann and Kuhn Mlcroregma heterostoma ,,"monlum Inhibition 1959b ,suitate Protozoan. Nickel 48 hr Incipient 820 8rIngmann et al. 1980; Chllomonas paramecium chlorIde Inhibition BrIngmann and Kuhn 1981 Protozoan. Nickel 20 hr Incipient 42 BrIngmann and Kuhn Uronema parduezl chiorIde InhibitIon 1980a. 1981Table6. (ConttnuecU Hardness (.-gil •• Concentration Species Ch_Ical Ca9C3) Duration Effect 

### c,g/U- Reference TubIfIcId worm, Nickel 34.2 48 hr lGSO 8.70 Brko.llc-Popcwlc and Tublfex tublfex suifate 7.00 PopovIe 19770 GIadoceran, Nickel 48 hr [GSO (rIver 6,000 BrIngmann and Kuhn Daphnia magna chloride water) 1959a,b GIadoceran, Nickel 48 hr EG50 (rIver 6,000 BrIngmann and Kuhn Daphnia magna CIlImonlum water) 1959a,b sulfate CIadoceran, Nickel 288 24 hr EC50 11,000 BrIngmann and Kuhn Daphnia magna chlorIde (swlnrnlng) 1977b Cladoceran, Nickel 45.3 48 hr [G50 (Immob11- 1,120 BlesInger and Dllphnlll magna chlorIde zatlon) (tad) ChrIstensell 1972 CIadoceran, Nickel 45.3 21 days EC50 (Immobll- 130 BlesInger lind Daphnia magna chlorIde zatIon) Christensen 1972 Cladoceran, Nickel 45.3 21 days 16% reproduc- 30 BlesInger and +-- Daphnla magna chloride t Ive ImpaIrment Christensen 1972 +-- CIadoceran, 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 CIMoceran, Nickel 25 48 hr LC50 (TOC

### = 2,171 LInd et al. ManuscrIpt Daphnia pullcarla suifate 39 mg/L) Cladoceran, Nickel 28 48 hr LC50 (TOC

### = 1,140 LInd et al. Manuscript Daphnia pullcarla suifate 15 mg/U Cladoceran, Nickel 28 48 hr LC50 <TOC 1,034 L1nd at al. ManuscrIpt Daphnia pullcarla suifate 13 mg/L) CIMoceran, Nickel 29 48 hr LC50 (TOC 697 L1nd at al. Manuscript Daphnia pullcarla sulfate 13 mq/UTable 6. (CoAtlnuecU Hardness (IIg/Las CoIIC_tret1011 Species Cta_lcal**C~)** Duration Effect Cpg/U- Reference CIadoceran, Nickel 73 48 hr LC50 (rOC

### = 3,414 Lind et al. ManuscrIpt Daphnia pullcarla suifate 28 mq/L) CIadoceran, Nickel 74 48 hr LC50 (rOC

### = 2,325 Lind et al. Manuscrlpt Daphnia pullcarla suifate 28 mg/L) CIadoceran, Nickel 84 48 hr LC50 <TOC 3,014 LInd et al. Manuscript Daphnia pullcarla suifate 32 mg/L) CIadoceran, Nickel 86 48 hr LC50 (rOC 3,316 LInd et al. Manuscript Daphnia pullcarla suifate 34 mg/L) Cladoceran, Nickel 89 48 hr LC50 <TOC 2,042 LInd et al. Manuscript Daphnia pullcarla suifate 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 suifate 34 mg/L) VI CIadocaran, Nickel 114 48 hr LC50 <TOC 3,156 Lind et al. Manuscript Daphnia pullcarla suifate 27 mg/L) CIadoceran, 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% survIvai 5,000 Lorz et al. 1978 Oncorhynchus klsutch chlorIde Rainbow trout (0.5-0.9 q) , Nil::kel 42 48 hr LC50 35,730 W II Iford 1966 galrdnerl sulfate RaInbow trout (1 yrl. NIckel 240 48 hr LC50 32,000 Brown and Dalton 1970 galrdnerl suifateTable6. (ContInuecU Hardness (Mg/l as ConcentratIon Species Che-Ical Cel Duration Effect (,s/U- R.f

....enc. RaInbow trout Nickel 104 28 days EC50 (d')dth 50 Birge 1978; Birge and (embryo, larva), chlorIde (92-110) and defonnIty) Black 1980; Birge et al. galrdnerl 1978,1979,1980,1981 RaInbow trout Nickel 125 28 days a:;50 (death 60 Birge et al. 1981 (embryo, Iarva), chlorIde and defonnlty) galrdnerl RaInbow trout Nickel 174 28 days 8;50 (death 90 Birge et al. 1981 (embryo, larva), chlorIde and deformIty) galrdnerl RaInbow trout, Nickel 240 3.5 days Decreased gill 2,000 Hughes et al. 1979 Salmo gaIrdnerI suifate d IffusIon RaInbow trout (ad1.11t), Nickel 320 6 mo Increase In 1,000 Ar1110 et al. 1982 galrdnerl chlorIde liver proteolytic cx:tlvlty of males
P- RaInbow trout (10 g), Nickel 28.4 20 min Avoidance n.9 Glattlna et al.1982 0' Salmo galrdnerl chloride threshoId RaInbow trout, Nickel 22.5 48 hr LC50 54,963 BornatowleI 1983 galrdnerl suitate RaInbow trout Nickel 50 38 days LC50 1.400 Nebeker et al. 1985 (5 days post hatch), chlorIde galrdnerl Brown trout lO.8-1.2 g), Nickel 42 48 hr LC50 60,290 Willford 1966 trutta suifate Brook trout (0.4-0.6 g), Nickel 42 48 hr LC50 54,040 Willford 1966 Salvellnus fontlnalls sulfate Lake trout (2.5-3.2 g), Nickel 42 48 hr LC50 16,750 Willford 1966 Salvellnus namaycush suifateTable6. (Continued) Hardness (ilg/l as Coftc_tratlOll Specie. Chellical**C~)** Duration Effect (Ps/U- R.t

......c. Goldfish, Nickel 19-50 hi" LT 100,000 Ellis 1937 CarassIus auratus chiorlde 200-210 hr LT 10,000 Goldfish (embryo, larva), Nickel 195 7 days EC50**(de~th** 2,140 BIrge 1978 Carasslus auratus chloride and defonnIty) GoldfIsh (embryo, larva), NIckel 93- 7 days EC50**(de~th** 2,780 BIrge and Black 1980; Carasslus auratus chiorlde 105 and defonnlty) Birge at al. 1981 CaMIOn carp (embryo), Nickel 128 72 hi" LC50 6,100 Blaylock and frank Cyprlnus carpIo suifate 1979 Canmon carp (larva), NIckel 128 72 hr LC50 8,460 Blaylock and frank Cyprlnus carp10 suifate 257 hr 750 1979 COlhIIon carp (embryo), Nickel 360 EC50 (hatch) 22,000 Kap

.... and Yadav 1982 Cyprlnus carpIo suifate FatheM minnow, NIckel 28 96 hr L.C50 HOC 2,923 LInd at al• Manuscript Plmephalas promelas suifate 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 suifate 32 mglL) Fathead minnow, NIckel 86 96 hr LC50 HOC == 5,}8} LInd et al. ManuscrIpt Plmephales promelas suifate 15 mg/U fathead mInnow, Nickel 89 96 hr L.C50 HOC 17,678 L1nd et al. Manuscript Plmephales promelas suifate }} 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 WIIIford 1966 Ictalurus punctatus suifate Channel catfish, NIckel 93- 7 days 8::50 (death 710 Birge md Black 1980; Ictalurus punctatus chlorIde 105 and defonnlty) Birge at al. 1981Tabl.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 (hIgh 34,900 Khangarot 1981 PoectIia retlculatlll suifate solids) Guppy (J84 mg), Nickel 260 48 hi" LC50 37,000 Khanglllrot at al. 1981 PoeclI IIII retlculatlll chloride BIuegIII (0.7-1.1 g), Nickel 42 48 hr LC50 110,500 Willford 1966 Lepomls macrochlrus suifate Largemouth bass Nickel 9,- 8 days EL50 (death 2,020 Birge and Black 1980; (embryo, Iarva), 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, Iarva)• chlorIde 103 and deformity) Gastrophryne caroltnensls +'- (Xl fowler's toad, Nickel 93- 7 days EC50 (death 11,030 Birge and Black 1980 Bufo fowlerl chloride 105 and deformity) Marblad saIamander Nickel 93- 8 days ELSO (death 420 Birge and Bhlck 1980; (embryo. IllIrva), Chloride 105 and deformity) (410) Birge at al. 1978 Ambystomlll opacumTebl. 6. (Continued) S.llnlty Ooncentrat10ft SpecI•• Ch_lc.1 (g/kg) Ountlon Effect Cps/U- R.ter.c. SALTWATER SPECIES Golden bro",," alga, 28 2 days Lowest concen- 500 WlIson and Freeberg 1980 Isochrysls galbana tratlon reducIng chlorophyll-! Golden bro",," alga, 28 9 days Lowest concen- 80 W IIson and Freeberg 1980 Isochrysls galbana tratlon reducing cell numbers DI,Hom, Nickel 26 7 days Reduced growth 1,000 Skaar et al. 1974 PhaeodactyIum trlcornutum chloride DIatom, 14 2 days Chlorophyll 100 WIIson 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 W IIson and Freeberg 1980 ThaIasslosIra pseudonana ralucal a>out 65% at 20°C DlatOOl, 14 2 days Chlorophyll a 17 Wilson and Freeberg 1980 Thalassloslra pseudonana rtducad a>ouT 65% at 24·C DlatOOl, 14 2 days Chlorophyll 80 WIIson and Freeberg 1980 Thalassloslra pseudonana reducad 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 WIIson and Freeberg 1980 Thalassloslra pS8udonana rwuced about 65S at 16°CTabl. 6. (Continued) Salinity 

### eonc....tnt1011 SfH!CI•• Ch_lcal (g/kg) Duration Effect 

### tes/L)· R.ter

....c.**DI~tom,** 28 2 days 0'11orophyI I a 30 WIIson and Fr86berg 1980 ThaIasslosIra eseudonana reduced abouT 65% at 20·C Diatom, 28 2 days Chlorophyll a 21 WII!Dn and Freeberg 1980 Thalassloslra eseudonana reduced about 65% at 24·C Diatom, 28 2 days Chlorophyll a 18 W IIson and Freeberg 1980 Thalassloslra eseudonana reduced abouT 65% at 28·C Diatom, 28 2 days Lowest concen- 100 W IIson and Freeberg 1980 Thalassloslra**eseudonan~** tratlon reducIng chlorophyll 

### oInoflagellate, 28 5 days Reduced chloro- 50 WIIson and Freeberg 1980 Glenodlnlum phyll and populatIon numbers In chemoVI stat cultures 0 DInoflagellate, 28 2 days Lowest concen- 200 wllson and Freeberg 1980 Glenodlnlum tratlon reducIng chlorophyll DInotIagelIate, 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 Wllson and Freeberg 1980 GymnodInium splendens reduced cbouT 65% at 20°C DInoflagellate, 28 2 days Chlorophyll 560 WIIson and Freeberg 1980 GymnodinIum splendens reduced about 65% at 24°CTable6. (Coatlnued) SalinIty eo.c.tratl_ Sp!Cles Ch_lcal (g/kg) Duration Effect (Ps/U· Reter.c. Dlnotlagellate, 26 2 days ChiorophyII 130 WIlson Md Freeberg 1960 GymnodInium splendens reduced about**65~** at 26·C 

### oInotIagellate, 26 2 days Chlorophyl

### i a 1,800 WlIson and Freeberg 1960 GymnOdInIum splendens reduced l:DouT 65. at 30·C 

### oInotIagellate, 14 2 days Chlorophyll a 1,800 W II9:>n and Freeberg 1960 GymnOdinIum splendens reduced abouT**65~** at 16·C olootIagellate, 14 2 days Chlorophyll 400 WII9:>R and Freeberg 1960 GymnodinIum splendens reduced about 65% at 30·C oloot1agellate, 26 2 days Lowest concen- 200 W IIson and Freeberg 1960 GymnOdInIum splendens tratlon reduclog Chlorophyll
V1 Polychaete worm (adult), Nickel 26 days InhIblted 100- Petrich and ReIsh 1979 Ctenodrllus serratus chloride reproduction 500 81ue mussel, Nickel 29- 10 weeks AlP reduced; no 10 ZaroogIan et al. 1962 MytlIus adulls chloride 32 effect on AEC PClCItIe oyster (juven11e), Nickel 34 14 days 19% reductIon 20 Watling 1963 Crassostrea chiorIde In growth Eastern oyster (larva), NiCkel 24+2 12 days LC50 1,200 Calabrese et al. 1977 Crassostrea vlrglnlca chloride Eastern oyster (larva), NIckel 24+2 12 days 54.6. reductIon 1,200 Calabrese et al. 1917 Crassostrea vlrglnlca chlorIde In growth Eastern oyster, NIckel 29- 10 weeks etfect on 10 Zarooglan et "I• 1982 Crassostrea vlrglnlca chlorIde 32 AEC and canponeots CIam (Iarva), NiCkel 35 48 hr Reduced calclum 2,000 Ii:> and Zubkott 1983 Mullna lateralls chior-Ide uptakeTabl. 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 Calabre58 et ale 1977 Mercenarla mercenarla chlorIde No growth 5,700 Common Pacific littleneck NICkel 31 48 hr BCF

### =4.3 Hardy and RoesljadI 1982 (adult), nUrate (gIII) Protothaca stamlnea Common PacIfIc littleneck Nickel 31 48 hr BCF

### =4.0 Hardy and RoesljadI 1982 (adult), nitrate (whole clam) Protothaca stamlnea Copepod (adult), NiCkel 30 

### n hr LC50 14,570 Lussler and Cardin 1985 Pseudodlaptomus coronatus chlorIde Copepod (adult), NiCkel 30 

### n hr LC50 6,006 Lussier and CardIn 1985 Acartla clausl chlorIde Copepod (adult), NiCkel 30 

### n hr LC50 747 LussIer and CardIn 1985 Acartla tonsa chloride \.Jl PInk shrImp (adult), Nickel 48 hr LC50 56,880 Portmann 1968 N Pandalus montagul suitate Green crab (adult), NiCkel 48 hr LC50 170,600 Portmann 1968 Ccsrclnus maenas suifate Sea urchin (embryo), NiCkel 21 hr Stunted 7,562 Waterman 1937 Arbacla punctulata Chloride development Sea urchin (embryo), NICkel 42 hr >50% mortal Ity 7,562 Waterman 1937 Arbacla punctulata chlorIde Sea urchin (embryo), NICkel 18-26 hr Totally 586,900 TlmourIan and Watchmaker Lytechlnus plctus chlorIde arrested 1972 dElvelopment Sea urchIn (embryo), NIckel 48 hr Abnonnal 586.9 TlmourIan and Watctvnaker Lytechlnus plctus chloride dElvelopment 1972eo.centr.tICNI (,S/L)- R.ferenc. Tabl.6. (Continued)
Specl•• Sea ITchln (gCl1lete). Strongylocentrotus purpuratus SalInIty (g/kg) Duration 300min Effect Depressed spem mot\Ilty 58.69 Tlmourlan and watchmaker 1971



## • Results are EDCpressed as nIckel. not as the chamIcal•

Vt W •• Incubated for 2 to 4 days atter El>Cposure.

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