~~EPA 

United Stat. 

Environmental Protection 

Agency 

Watar 

Ambient 

Office of Water EPA~/5-87-008 

Regulations and Standards September 1987 

Criteria end Standardl Division 

washington. DC 20460 

Water Quality 

Criteria. for 

Selenium - 1987 
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR 

SELENIUM 

U.S. ENVIRONMENTAL PROTEC~ION 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 Regulations 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. 

Order number: PB88-142 237 

i i 
FOREWORD 

Section 304(a)(l) 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 gr6ups, and individual scientists. Criteria 

contained in this document replace any previously published EPA aquatic life 

crite~ia for the same pollutant(s). 

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

Water Act, section 304(a)(l) 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. 

Guidance 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 has been developed by EPA. 

William A. Whittington 

Director 

Office of Water Regulations and Standards 

i i i 
ACKNOWLEDGMENTS 

Loren J. Larson 

Larry T. Brooke 

(freshwater contributors) 

University of Wisconsin-Superior 

Superior, Wisconsin 

Charles E. Stephan 

(document coordinator) 

Environmental Research Laboratory 

Duluth, Minnesota 

Jeffrey L. Hyland 

Jerry M. Neff 

(saltwater contributors) 

Battelle Ocean Sciences 

Duxbury, Massachusetts 

David J. Hansen 

(saltwater coordinator) 

Environmental Research Laboratory 

Narragansett, Rhode Island 

iv 
CONTENTS 

Foreword... . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . iii 

Acknowledgments. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . i v 

Tables ................................................................... vi 

Introduction ............................................................ . 

Acute Toxicity to Aquatic Animals........................................ 7 

Chronic Toxicity to Aquatic Animals ...................................... 12 

Toxicity to Aquatic Plants............................................... 18 

Bioaccumulation.......................................................... 20 

Other Data.·.............................................................. 23 

Unused Data .... ·....................................................... . . . 29 

Summary.. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 32 

National Criteria ........................................... :'............ 34 

Implementation........................................................... 35 

Re fe renee s. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 78 

v 

• 
TABLES 

Page 

t. Acute Toxicity of Selenium to Aquatic Animals .................... 40 

2. Chronic Toxicity of Selenium to Aquatic Animals.................. 51 

3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic 

Ratios. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 54 

4. Toxicity of Selenium to Aquatic Plants........................... 61 

5. Bioaccumulation of Selenium by Aquatic Organisms ................. 64 

6. Other Data on Effects of Selenium on Aquatic Organisms ........... 67 

vi 
Introduction 

Selenium is unique among pollutants because of its following attributes: 

1. Selenium is located immediately below sulfur in group 6A in the periodic 

table. Thus selenium is a metalloid, not a metal. More importantly, the 

chemical and physical properties of selenium and sulfur are so similar 

that these elements are related in a variety of ways. For example, 

selenium can replace sulfur in some minerals and biologically important 

compounds ( Ca 11 a han et a 1. 1979; Cooper et a 1. 1974; Ewan 1979; Sham berger 

1983). Also, sulfate reduces the toxicity of selenium to some species 

(Bennett et al. 1986; Ewan 1979; Halverson and Monty 1960; Kumar and 

Prakash 1971; Martin 1973; Sarma and Jayaraman 1984; Shrift 1954a,b, 1961; 

Wheeler et al. 1982). However, if selenium and sulfur were 

physiologically and toxicologically interchangeable, selenium would not be 

more toxic than sulfur (Brown and Shrift 1982; Shamberger 1983; Shrift 

1973). Some of the proposed ·modes of action of selenium involve reaction 

with or substitution for the sulfur in such biologically relevant natural 

compounds as sulfur-containing amino acids (Foe and Knight, Manuscript; 

Magos and Webb 1980). 

2. Substantial quantities of selenium enter surface waters from both natural 

and anthropogenic sources. It is abundant in the drier soils of North 

America from the Great Plains to the Pacific Ocean. Some ground waters in 

California, Colorado, Kansas, Oklahoma, South Dakota, and Wyoming contain 

elevated concentrations of selenium due to weathering of and leaching from 

rocks and soils. Selenium also occurs in sulfide deposits of copper, 

lead, mercury, silver, and zinc and can be released during the mining and 

smelting of these ores. In addition, selenium occurs in high concentrations in coal and fuel oil and is emitted in flue gas and in fly 
ash during combustion. Some selenium then enters surface waters in 

drainage from fly-ash ponds and in runoff from fly-ash deposits on land. 

3. Three oxidation states (selenide = -2, selenite = +4, and selenate = +6) 

can exist simultaneously in aerobic surface water at pH= 6.5 to 9.0. A 

fourth oxidation state (elemental = 0) exists in sediment, but is 

insoluble in water. Chemical conversion from one oxidation state to 

another often proceeds at such a slow rate in aerobic surface water that 

thermodynamic considerations do not determine the relative concentrations 

of the oxidation states. Thus although selenium(VI) is thermodynamically 

favored in oxygenated alkaline water, substantial concentrations of both 

selenium(-11) and selenium(IV) are not uncommon (Burton et al. 1980; 

Cutter and Bruland 1984; Measures and Burton 1978; North Carolina 

Department of Natural Resources and Community Development 1986; Robberecht 

and Van Gricken 1982; Takayanagi and Cossa 1985; Takayanagi and Wong 

1984a,b; Uchida 1980). 

4. Living organisms can affect selenium in a variety of ways, and Shrift 

(1964) postulated a selenium cycle in which some species reduce the most 

oxidized form and others oxidize the reduced form(s). For example, 

organisms can oxidize elemental selenium to selenium( IV) (Sarathchandra 

and Watkinson 1981), reduce selenium(VI) to selenium(IV) (Lipinski et al. 

1986), produce gaseous dimethyl selenide and dimethyl diselenide (Chau et 

al. 1976; Doran 1982; Reamer and Zoller 1980), and reduce selenium(IV) and 

selenium(VI) to selenium(-11) and incorporate it into amino acids and 

proteins, such as selenomethionine (Bottino et al. 1984; National Research 

Council 1976; Stadtman 1974; Wrench 1978,1979). 

5. Although selenium can be quite toxic, it has been shown to be an essential 

trace nutrient for many aquatic and terrestrial species and it 

2 
ameliorates the effects of a variety of pollutants. Selenium deficiency 

has been found to affect humans (Fishb~in 1984; Frost and lngvolstad 

1975; Raptis et al. 1983; Wilber 1980,1983), sheep and cattle (Shamberger 

1983), fish (Bell et al. 1984,1985,1986; Fjolsand and Heyarass 1985; 

Gatlin 1983; Gatlin and Wilson 1984; Heisinger and Dawson 1983; Hilton et 

al. 1980; Hodson and Hilton 1983; Ostroumova 1986; Poston et al. 1976; 

Wilson et al. 1984), an aquatic invertebrate (Cowgill et al. 1985,1986; 

Keating and Dagbusan 1984), and algae (Lindstrom 1984; Wehr and Brown 

1985). In addition, selenium protects biota from the toxic effects of 

arsenic, cadmium, copper, inorganic and organic mercury, silver, and the 

herbicide paraquat in both aquatic and terrestrial environments (Beijer 

and Jernelov 1978; Eisler 1985; Ganther 1980; Heisinger and Scott 1985; 

Heisinger et al. 1979; Hutchinson and Stokes 1975; Kim et al. 1977; 

Levander 1977; Magos and Webb 1980; Pelletier 1986b; Shamberger 1983; 

Skerfving 1978; Van Puymbroeck e~ al. 1982; Wilber 1983; Winner 1984). 

Birge et al: (1978,1979a,b,1981) and Huckabee and Griffith (1974), 

however, reported that selenium and mercury acted synergistically toward 

fish embryos. Selenium pretreatment protected 128-hr old, but not 6-hr 

old, embryos of Oryzias latipes from cadmium and mercury (Heisinger 

1981), whereas prior exposure to selenium did not affect the sensitivity 

of white suckers to cadmium (Duncan and Klaverkamp 1983). Selenium is 

reported to reduce the uptake of mercury by some aquatic species 

(Klaverkamp et al. 1983; Moharram et al. 1987; Rudd et al. 1980; Turner 

and Rudd 1983; Turner and Swick 1983), to have no effect on uptake of 

mercury by a mussel (Pelletier 1986a), and to increase the uptake of 

mercury by mammals and some fish (Heisinger et al. 1979; Kim et al. 1977; 

Luten et al. 1980; MacKay et al. 1975; Ringdal and Julshamn 1985; Shultz 

3 
and Ito 1979). Selenium augmented accumulation of cadmium in some tissues 

of the shore crab, Carcinus maenas (Bjerregaard 1982,1985). The available 

data do not show whether the various inorganic and organic compounds and 

oxidation states of selenium are equally effective sources of selenium as 

a trace nutrient or as protection against pollutants. 

6. Not only has selenium been demonstrated to be toxic to aquatic species 

when it is dissolved in water, it has also been demonstrated that uptake 

of selenium from food can adversely affect aquatic species (e.g., Bennett 

et al. 1986; Goettl and Davies 1978; Hicks et al. 1984; Hilton et al. 

1980; Hodson and Hilton 1983) and mallard ducks (Heinz et al. 1987; 

Hoffman and Heinz 1987). 

• 7. In some situations aquatic organisms accumulate more selenium from food 

than from water (Birkner 1978; Fowler and Benayoun 1976a,b,c; Rudd et al. 

1980; Sandholm et al. 1973; Turner and Swick 1983). Turner and Swick 

(1983) al$0 found that under some conditions pike accumulated equal 

amounts from food and water. Shrimp lost selenium that had been 

accumulated from water faster than that accumulated fro~ food (Fowler and 

Bena.youn 1976a). 

8. Selenium(-11) as selenomethionine is sometimes more biologically active 

than either selenium(IV) or selenium(VI). Fish accumulated 

selenomethionine more efficiently than selenium( IV) or selenium(VI) from 

both the gastrointestinal tract (Kleinow 1984; Kleinow and Brooks 1986a) 

and from water (Sharma and Davis 1980). Sandholm et al. (1973) found that 

algae accumulated selenomethionine much more than selenium(IV), but the 

opposite was true for daphnids and fish. Also, Kumar and Prakash 

(1971) and Niimi and LaHam (1976) reported that selenium as 

selenomethionine was more toxic to algae and fish, respectively, than 
were selenium(IV) and selenium(VI). Selenopurine was as toxic to algae as 

selenomethionine (Kumar and Prakash 1~71), but selenocystine was less 

toxic to fish (Niimi and LaHam 1976). Heinz et al. (1987) and Hoffman and 

Heinz (1987) found that selenium as selenomethionine is more toxic to 

mallards than selenium(IV) and that mallards contained more selenium in 

eggs, liv~r. and breast muscle when fed selenomethionine than when fed 

s e I en i um ( IV) . 

9. The concentration of selenium in specific tissues can depend on the 

exposure route, concentration, and form of selenium. For example, Lemly 

{1982) found relatively low concentrations of selenium in gonads of 

centrarchids exposed to selenium{ IV) in laboratory tests, whereas Cumbie 

and Van Horn (1978) found high concentrations in gonads of centrarchids 

from Belews Lake, which contained a moderately high concentration of 

selenium. In another case, at low levels of selenium(IV) in food or 

water, the kidneys of rainbow trout contained more selenium.than the 

livers, whereas the converse was true at higher concentrations (Hilton et 

al. 1982; Hodson and Hilton 1983; Hodson et al. 1980). Similarly, .. he 

relative distribution of selenium in tissues of shrimp depended on whether 

the selenium was accumulated from water or from food (Fowler and Benayoun 

1976b). Also, Heinz et al. (1987) found that when mallards were fed 

selenium(IV), more selenium was deposited in the egg yolk than in the egg 

white. When mallards were fed selenomethonine, however, more selenium was 

found in the white than in the yolk. In addition, the relative 

distribution between tissues might depend on the duration of the exposure 

and on whether the organisms are in the uptake or depuration phase 

{Kleinow and Brooks 1986a). 

5 
10. Selenium occurs in a variety of forms in organisms. Because of "alkali 

disease" and "blind staggers" among livestock, the characterization of 

selenium in terrestrial plants has received much attention. The 

water-soluble fraction from plants contained selenite, selenate, 

seleno-amino acids, and possibly other compounds. After treatment of the 

insoluble fraction with proteolytic enzymes, various seleno-amino acids 

were found (Allaway et al. 1967;. Brown and Shrift 1982; Olson et al. 

1970). Selenium in algae has been found in free and combined amino acids 

(Bottino et al. 1984; Burton et al. 1960; Wrench 1978) and bound to lipids 

(Gennity et al. 1964). Similarly, saltwater animals contained selenium in 

proteins and lipids (Braddon-Galloway and Sumpter 1986; Lunde 1973; Maher 

1985; Wreneh 1979). Cappon (1984) and Cappon and Smith (1981,1962a,b) 

' 

found that 8 to 477. of the selenium in the edible portions of various 

freshwater and saltwater species was selenium(VI) artd that 35 to 807. was 

water·-soluble. 

Although other pollutants possess some of these attributes, selenium is the 

only pollutant for which all of these have been demonstrated. Many of these 

attributes make it difficult to design and conduct tests on selenium and to 

decide how ~he data should be interpreted and used to derive aquatic life 

water quality criteria for selenium. On the other hand, comparison of the 

form and location of selenium in affected and unaffected organisms from 

laboratory and field exposures might be helpful in determining the route by 

which aquatic organisms in field situations accumulate toxic amounts of 

selenium. 

Unless otherwise noted, all concentrations of selenium in water reported 

herein from toxicity and bioconcentration tests are expected to be essentially 

equivalent to acid-soluble selenium concentrations. All concentrations are 

6 
expressed as selenium, not as the chemical tested. Although VI is expected to 

be the predominant oxidation state at chemical equilibrium in oxygenated 

alkaline water, the rate of conversion of IV to VI seems to be slow in most 

natural waters. Therefore, it was assumed that when IV was introduced into 

stock or test solutions, it would persist as the predominate state throughout 

the test, even if no analyses specific for the IV oxidation state were 

performed. Similarily, it was assumed that when VI was introduced into stock 

or test solutions, it would persist as the predominant state throughout the 

test, even if no analyses specific for VI were performed. 

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), hereinafter referred to as the Guidelines, and the 

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

understand the following text, tables, and calculations. Results of such 

intermediate calculations as recalculated LC50s and Species Mean Acute Values 

are given to four significant figures to prevent roundoff error in subsequent 

calculations, not to reflect the precision of the value. The criteria 

presented herein supersede previous national aquatic life water quality 

criteria for selenium (U.S. EPA 1976,1980a) because these new criteria were 

derived using improved procedures and additional information. The latest 

comprehensive literature search for information for this document was 

conducted in July, 1986; some more recent information was included. 

Acute Toxicity to Aquatic Animals 

Selenium( IV) 

Data that may be used, according to the Guidelines, in the derivation of 

Final Acute Values for selenium(IV) and selenium(VI) are presented in Table 

7 
1. The LC50 for selenium(IV) sometimes decreased substantially as the 

duration of the test increased. For example, Halter et al. (1980) reported 

the LC50 for the amphipod, Hyalella azteca, to be 940 pg/L at 2 days, 

340 pg/L at 4 days, and 70 pg/L at 14 days. (Although Halter et al. 

(1980) did not specify the oxidation state used in their studies, Adams and 

Johnson (1981) stated that the tests were conducted on sodium selenite.) 

Similarly, Adams (1976) reported that the average LC50 for the rainbow trout, 

Salmo gairdneri, was 4,350 pg/L at 4 days, 500 pg/L at 48 days, and 

280 pg/L at 96 days, and for the fathead minnow, Pimephales promelas, the 

average LC50 was 10,900 pg/L at 4 days and 1,100 at 48 days. 

Adams (1976) found that the acute toxicity of selenium( IV) to the fathead 

minnow was related to water tempe;ature with average 96-hr LC50s of 

10,900 pg/L at 13°C, 6,700 pg/L at 20°C, and 2,800 pg/L at 

25°C. A daphnid, a midge, and the striped bass, Morone saxatilis were more 

sensitive to selenium{IV) in soft than in hard water (Mayer and Ellersieck 

1986; Palawski et al. 1985). These results might be explained by the findings 

of ~emly (1982) that both temperature and hardness influenced the rate of 

uptake of selenium by centrarchids in short exposures, but that neither 

temperature nor hardness had a significant effect on the final concentration 

in any tissue after exposure to selenium(IV) for 120 days. 

Invertebrates are both the most sensitive and most resistant freshwater 

species to selenium(IV) with acute values ranging from 210 pg/L for the 

crustacean, Daphnia magna (Adams and Heidolph 1985) to 203,000 pg/L for the 

leech, Nephelopsis obscura (Brooke et al. 1985). The acute values for fishes 

range from 620 pg/L for the fathead minnow (Kimball, Manuscript) to 

35,000 pg/L for the common carp, Cyprinus carpio (Sato et al. 1980). 

8 
Boyum (1984) reported a 48-hr LC50 of 6 ~g/L for Daphnia pulicaria. 

Other acute values reported for species in the genus Daphnia ranged from 

210 ~g/L (Adams and Heidolph 1985) to 3,870 ~g/L (Reading 1979; Reading 

and Buikema 1983), so the value of 6 ~g/L is surprisingly low. Boyum 

(personal communication, 14 February 1986) stated that the survival of Daphnia 

pulicaria in the lowest concentration tested was only 47% in the test that 

produced the LC50 of 6 ~g/L. Because of the high mortality at the lowest 

concentration, the value of 6 ~g/L was not considered acceptable for use in 

calculating a criterion. However, the results of this and similar unreported 

tests by Boyum (personal communication, 14 February 1986) indicate that the 

acute value for this species might be less than 100 ~g/L. 

Just as the nine acute values for Daphnia magna cover a rather large 

range from 210 to 2,500 ~g/L, the acute values for the fathead minnow range 

from 620 to 11,300 ~g/L. The values reported by Kimball (Manuscript) were 

the lowest for the fathead minnow, but not for Daphnia magna. The seven acute 

values for the rainbo~ trout range from 1,800 to 12,500 ~g/L. 

Freshwater Species Mean Acute Values (Table 1) were cal~ulated as 

geometric means of the available acute values for selenium(IV), and Genus Mean 

Acute Values (Table 3) were then calculated as geometric means of the Species 

Mean Acute Values. Of the twenty-two genera for which freshwater mean acute 

values are available, the most sensitive genus, Hyalella, is 597 times more 

' sensitive than the most resistant, Nephelopsis. The range of sensitivities of 

the four most sensitive genera is a factor of 5. The freshwater Final Acute 

Value for selenium(IV) was calculated to be 371.8 ~g/L using the procedure 

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

Final Acute Value is higher than the lowest Species Mean Acute Value. 

9 
Acute toxicity data that can be used to derive a saltwater criterion for 

selenium(IV) are available for eight speci~s of invertebrates and eight 

species of fish that are resident in North America (Table 1). The range of 

acute values for saltwater invertebrates extends from 850 ~g/L for adults 

of the copepod, Acartia tonsa (Lussier 1986) to greater than 10,000 ~g/L 

for embryos of the blue mussel, Mytilus edulis (Martinet al. 1981) and 

embryos of the Pacific oyster, Crassostrea gigas (Glickstein 1978; Martinet 

al. 1981). The range of acute values for fish is slightly wider than that for 

invertebrates, extending from 599 ~g/L for larvae of the haddock, 

Melanogrammus aeglefinus, to 17,350 ~g/L for adults of the fourspine 

stickleback, Apeltes guadracus (Cardin 1986). No consistent relationship was 

detected between life stage of invertebrates or fish ~nd their sensitivity to 

selenium(IV), and few data are available concerning the influence of 

temperature or salinity on the toxicity of selenium(IV) to saltwater animals. 

Acute tests with the copepod, Acartia tonsa, at·5 and 10°C gave similar 

results (Lussier 1986). 

Of the fifteen genera for which saltwater mean acute values are available 

(Table 3), the most sensitive genus, Melanogrammus, is nearly 29 times more 

sensitive than the most resistant, Apeltes. The sensitivities of the four 

most sensitive genera differ by a factor of only 2.1. and these four include 

three invertebrates and one fish, which is the most sensitive of the four. 

The saltwater Final Acute Value for selenium(IV) is 587.7 ~g/L, which is 

slightly lower than the lowest Species Mean Acute Value. 

Selenium(VI) 

Among freshwater invertebrates, amphipods and cladocerans are quite 

sensitive to selenium(VI). Gammarus pseudolimnaeus, with a mean acute value 

of 65.38 ~g/L, is the most sensitive tested freshwater species, and another 

10 
amphipod, Hyalella azteca, with an LC50 of 760 ~g/L, is the third most 

sensitive species. The EC50 for Daphnia qulicaria is 246 ~g/L (Boyum 1984) 

whereas the EC50s for Daphnia magna range from 570 to 5,300 ~g/L from three 

independent studies. 

The fathead minnow is the most sensitive freshwater fish species with 

which an acute test has been conducted on selenium(VI). Five 96-hr exposures 

resulted in LC50s ranging from 2,300 to 12,500 ~g/L. One test (Spehar 

1986) was a flow-through test in which the concentrations were measured. The 

tests conducted with the fathead minnow in the hardest water (323 mg/L as 

CaC03 ) gave 96-hr LC50s from 11,000 to 12,500 ~g/L (Table 1) and a 48-day 

LC50 of 2,000 ~g/L (Table 6). The hydroid, Hvdra sp., was about as 

sensitive to selenium(VI) as the fathead minnow (Table 1). Other species were 

quite resistant with LC50s ranging from 20,000 ~g/L for a midge, 

Paratanytarsus parthenogeneticus, to 442,000 ~g/L for a leech, Nephelopsis 

obscura. · 

Of the eleven genera for which freshwater mean acute values are available 

for selenium(VI), the most sensitive, Gammarus, is 6,760 times more sensitive 

than the most resistant, Nephelopsis. The range of sensitivities of the four 

most sensitive genera is a factor of 84. The freshwater Final Acute Value for 

selenium(VI) was calculated to be 25.65 ~g/L. This Final Acute Value is 

substantially below the acute value of the most sensitive freshwater species, 

because data are available for only eleven genera and because of the large 

differences between the values for the four most sensitive genera. 

The only species with which acute tests have been conducted on 

selenium(VI) in salt water is the striped bass (Table 1). Klauda (1985) 

obtained 96-hr LC50s of 9,790 and 85,840 ~g/L with prolarvae and juvenile 

striped bass, respectively. 

11 
Species Mean Acute Values have been determined for both selenium(IV) and 

selenium(VI) with ten freshwater species (Table 3) and one saltwater species 

(Table 1). For ten of these eleven species selenium(IV) is 1.6 to 6.3 times 

more toxic than selenium(VI). For the freshwater Gammarus pseudolimnaeus, 

however, selenium(VI) is 41 times more toxic. Acute tests were conducted on 

both selenium(IV) and selenium(VI) with this gammarid by the same 

investigators in 1985 and in 1987 (Brooke 1987; Brooke et al. 1985). This 

species is moderately sensitive to selenium(IV) but is very sensitive to 

selenium(VI). The Final Acute Value for selenium(VI) is fourteen times lower 

than that for selenium(IV) because fewer Genus Mean Acute Values are available 

for selenium(VI) and because of the low acute value obtained with Gammarus 

pseudolimnaeus. • 

Chronic Toxicity to Aquatic Animals 

Selenium( IV) 

The available data that are usable according to the Guidelines concerning 

the chronic toxicity of selenium(IV) and selenium(VI) are presented in Table 

2. Chronic toxicity tests have been conducted on selenium(IV) with five 

freshwater species, four of which are acutely sensitive species (Table 3). 

The rainbow trout is both the most acutely resistant of these five species, 

and the most chronically sensitive, and thus has a much larger acute-chronic 

' ratio than the other four species. Goettl and Davies (1977) exposed rainbow 

trout to selenium(IV) for 27 months, and they found that survival of fish 

exposed to 60 ~g/L was similar to survival of control fish. Survival of 

fish exposed to 130 ~g/L was about 507. of that of the controls and about 

167. of these survivors were deformed, even though no control fish were 

deformed. Hodson et al. (1980) found that 47 to 53 ~g/L caused a small 

12 
reduction in percent hatch of rainbow trout, but did not reduce survival of 

sac or swim-up fry. The small reduction ~n percent hatch is not considered 

unacceptable for the purposes of deriving water quality criteria. The data of 

Goettl and Davies (1977) indicated that the acute-chronic ratio was less than 

187.2, and the data of Hodson et al. (1980) gave a ratio of 141.5. 

In 90-day exposures starting with newly hatched fry, Hunn et al. (1987) 

found that selenium(IV) at concentrations of 12 ~g/L and greater 

significantly reduced the concentration of calcium in bone of rainbow trout. 

However, the expected resulting decrease in the toughness and/or strength of 

the bone did not occur. A 90-day LC50 of 55.2 ~g/L was calculated from the 

published data on percent survival, allowing for 8.9% spontaneous mortality 

(Table 6). The Guidelines (page 17) specify division of an LC50 by 2 to 

calculate a concentration that will not severely affect too many of the 

organisms. Division of 55.2 ~g/L by 2 results in 27.6 ~g/L. 

The other four freshwater species with which chronic tests have been 

conducted on selenium(IV), including one fish species, are a'll acutely more 

sensitive, and chronically more resistant, than the rainbow trout. Kimball 

(Manuscript) conducted an early life-stage test on selenium(IV) with fathead 

minnows. A selenium(IV) concentration of 153 ~g/L reduced survival by 32% 

and reduced weight by 18.5%. At a concentration of 83 ~g/L, survival was 

reduced by 2% and weight was reduced by 9.6%. The resulting chronic value and 

' acute-chronic ratio were 112.7 ~g/L and 6.881, respectively. 

Kimball (Manuscript) also studied the effects of selenium(IV) on survival 

and reproduction of Daphnia magna in a 28-day renewal test. Survival and 

reproduction of Daphnia magna exposed to 70 ~g/L were similar to those of 

control animals. Survival at 120 ~g/L was 100%, but reproduction, 

expressed as mean young per adult, was reduced 27% compared to the control 

13 
animals. The chronic value and acute-chronic ratio were 91.65 ~g/L and 

13.31, respectively. Adams and Heidolph (1985) also reported results of a 

life-cycle test with Daphnia magna on selenium(IV). The test was at a 

hardness of 240 to 310 mg/L and the chronic value was 161.5 ~g/L. An 

acute-chronic ratio cannot be calculated from this chronic value, however, 

because it appears that the acute test reported by Adams and Heidolph (1985) 

was conducted in a different water. 

Owsley (1984) and Owsley and McCauley (1986) reported the results of an 

exposure of four successive generations of the cladoceran, Ceriodaphnia 

affinis, to selenium(IV), but the concentrations in the test solutions were 

not adequately measured. A concentration of 200 ~g/L severely affected all 

four generations, and the amount of effect increased with each successive 

generation. A concentration of 100 ~g/L caused an unacceptable effect on 

only the second generation. The chronic value from this test would probably 

be close to 100 ~g/L, and the acute-chronic ratio would be close to 6. 

Reading (1979) and Reading and Buikema (1983) reported the chronic 

effects of selenium(IV) on the survival, growth, and reprodiction of Daphnia 

pulex in a 28-day renewal test. At the end of the test, survival, total 

number of young per adult, and mean brood size at 600 ~g/L were equal to or 

greater than those of the control daphnids, even though some differences were 

observed for some broods during the test. A concentration of 800 ~g/L 

caused about a 40% reduction in the mean total number of live young per 

adult. The resulting chronic value was 692.8 ~g/L and the acute-chronic 

ratio was 5.586. 

Data on the chronic toxicity of selenium(IV) are available for two 

saltwater species, the mysid, Mysidopsis bahia, and the sheepshead minnow, 

Cyprinodon variegatus (Table 2). The life-cycle test with Mysidopsis bahia 

14 
was started with 48-hr post-release juveniles and lasted for 28 days (Ward et 

al. 1981). Exposure to concentrations of 320 ~g/L or greater significantly 

reduced survival of the first-generation mysids. No offspring were produced 

by mysids that survived exposure to 580 ~g/L. and the number of offspring 

produced per female was significantly lower in 320 ~g/L than in the control 

treatment. All offspring produced in all treatments survived until the end of 

the test. At 140 ~g/L, survival and reproduction were reduced 18% and 22%, 

respectively, compared to the controls, but these reductions were not 

statistically significant. The chronic value for Mysidopsis bahia is 

211.7 ~g/L and the acute-chronic ratio is 7.085. 

An early life-stage test was performed with the sheepshead minnow (Ward 

et al. 1981). The test was started with newly-fertilized eggs and extended 

for two weeks after hatch to measure survival and growth of juveniles. 

Percent hatch was reduced 0 to 4% by concentrations of 970, 1,900, and 

3,600 ~g/L. Survival of juveniles was reduced ·4% by 470 ~g/L, 24% by 

970 ~g/L, and more than 90% at higher concentrations. Growth was reduced 

8% by selenium concentrations of 470 and 970 ~g/L. The resulting chronic 

value for Cyprinodon variegatus is 675.2 ~g/L and the acute-chronic ratio 

is 10.96. 

Acute-chronic ratios· have been determined for selenium( IV) with three of 

the seven most acutely sensitive freshwater species. These ratios range from 

5.586 to 13.31 (Table 3). The two acute-chronic ratios that were determined 

with saltwater species also fall within this range. The Final Acute-Chronic 

Ratio of 8.314 was calculated as the geometric mean of these five ratios. The 

high acute-chronic ratio obtained with the rainbow trout was not used in the 

calculation of the Final Acute-Chronic Ratio because this is an acutely 

resistant species. Division of the Final Acute Values by the Final 

15 
Acute-Chronic Ratio results in freshwater and saltwater Final Chronic Values 

of 44.72 and 70.69 ~g/L, respectively. Based on the data reported by Hunn 

et al. (1987) for rainbow trout, the freshwater Final Chronic Value is lowered 

to 27.6 ~g/L to protect this important species. The saltwater Final 

Chronic Value is quite a bit lower than the two saltwater chronic values, but 

neither of the saltwater species with which chronic tests have been conducted 

is acutely sensitive to selenium(IV). 

Selenium(VI) 

Chronic tests have been conducted on selenium(VI) with three freshwater 

species (Table 2). Some additional chronic tests have been conducted by 

exposing freshwater animals to selenium(VI) in food and water simultaneously. 

Dunbar et al. (1983) conducted a 32-day renewal life-cycle test with Q. 

magna. Selenium(VI) at concentrations of 1,730 and 2,310 ~g/L reduced the 

total young production by 3.3 and 257., respectively. The chronic value was 

1,999 and the acute-chronic ratio was 2.651. 

·Boyum (1984) conducted three life-cycle tests on selenium(VI) with 

daphnids but did not measure the concentrations of selenium in any of the 

tests. In all three tests, the nominal concentrations of selenium were 0, 50, 

100, 500, and 1,000 ~g/L. In one test with Daphnia magna and in one test 

with Q. pulicaria, the animals were fed algae that had grown for 48 hours in 

the same concentration of selenium(VI) to which the daphnids themselves were 

exposed. In the third test, Q. magna was fed algae that had been raised in 

control water. In this third test, the intrinsic growth rate was reduced 527. 

at the concentration of 50 ~g/L. In the tests in which the algae contained 

selenium, the intrinsic growth rates of Q. magna and Q. pulicaria were reduced 

8.6 and 13%, respectively, by 50 ~g/L. When the daphnids were fed algae 

that contained selenium, Q. pulicaria was affected more than Q. magna at each 

16 
concentration of selenium. Also at each concentration of selenium, Q. magna 

was affected less when it received selenium from both food and water than when 

it received selenium from only water. Separate tests showed that 

selenomethionine in water and selenium in algae independently reduced the 

uptake of selenium(VI) from water by Q. magna. 

Daphnia magna was much more sensitive to selenium(VI) in the tests 

reported by Boyum (1984) than in those reported by Dunbar et al. (1983). It 

is interesting that the dilution water used by Boyum contained 21.5 mg 

sulfate/L, whereas that used by Dunbar et al. contained about 174 mg 

sulfate/L. 

Spehar (1986) reported results of a 90-day early life-stage test with 

rainbow trout. No fish survived at 6,300 ~g/L or higher concentrations. A 

concentration of 3,800 ~g/L reduced survival and weight by 93% and 24%, 

respectively. Survival and weight were reduced 7% and 12% by 2,200 ~g/L. 

The chronic value was 2,891 ~g/L and the acute-chr6nic ratio was 16.28. 

Spehar (1986) also reported results of a 32-day early life-stage test with 

the fathead minnow. No fish survived at 2,900 ~g/L, and 1,520 ~g/L 

reduced both survival and weight by more than 60%. At 820 ~g/L, survival 

was as good as in the control treatment, but weight was reduced by 34%. 

Weight was reduced only 3% by 390 ~g/L. Thus this test resulted in a 

chronic value of 565.5 ~g/L and an acute-chronic ratio of 9.726. Brooks et 

~ 

al. (1984) exposed fathead minnows throughout a life cycle to selenium(VI) in 

the range of 40 to 50 ~g/L. ·The fish were fed a food that was specially 

prepared (see also Bertram and Brooks 1986) to simulate a food chain in water 

that contained the same concentration of selenium(VI). Although a malfunction 

of the diluter caused the concentration of selenium to be 2 to 5 times higher 

for up to one week, no adverse effects on survival, growth, or reproduction 

were observed. 

17 
The three available acute-chronic ratios for selenium(VI) show a 

consistent pattern in that the more acutely sensitive species have a lower 

ratio (Table 3). Because it is meant to apply to sensitive species, the Final 

Acute-Chronic Ratio was set equal to 2.651, the ratio obtained with the most 

acutely sensitive species with which a chronic test has been conducted. 

Division of the freshwater Final Acute Value for selenium(VI) by the Final 

Acute-Chronic Ratio results in a freshwater Final Chronic Value of 

9.676 ~g/L, which is substantially below the three available experimentally 

determined chronic values. 

No data are available concerning the chronic toxicity of selenium(VI) to 

saltwater animals. 

Chronic toxicity tests have been conducted on both selenium(IV) and 

selenium(VI) with three species (Table 2). With all three species, 

selenium(IV) was 5 to 32 times more toxic than selenium(VI), which is similar 

to the relative acute toxicities of these two oxidation states. Nine Species 

Mean Acute-Chronic Rati~s are available for the two oxidation states (Table 

3) .. The ratio determined for selenium(IV) with rainbow trout is 141.5, but 

the other eight ratios are all between 2.6 and 17. 

Toxicity to Aquatic Plants 

Selenium( IV) 

~ 

Data are available on the toxicity of selenium(IV) to nine species of 

freshwater algae (Table 4). Results ranged from an LC50 of 30,000 pg/L for 

the blue-green alga, Anacystis nidulans (Kumar and Prakash 1971) to 

522 ~g/L for incipient inhibition of the green alga, Scenedesmus 

guadricauda (Bringmann and Kuhn 1977a,1978a,b,1979,1980b). Foe and Knight 

(Manuscript) found that 75 pg/L decreased the dry weight of Selenastrum 

18 
capricornutum (Table 6). Wehr and Brown (1985) reported that ·320 ~g/L 

increased the growth of the alga Chrysochromulina breviturrita. Thus the 

sensitivities of freshwater algae to selenium(IV) cover about the same range 

as the acute and chronic sensitivities of freshwater animals. 

The 96-hr EC50 for the saltwater diatom, Skeletonema costatum, is 

7,930 ~g/L, based on reduction in chlorophyll.!. (Table 4). Growth of 

Chlorella sp., Platymonas subcordiformis, and Fucus spiral is increased at 

selenium(IV) concentrations from 10 to 10,000 ~g/L (Table 6).· These data 

suggest that saltwater plants will not be adversely affected by concentrations 

of selenium(IV) that do not affect saltwater animals. 

Selenium(Vt) 

Growth of several species of green algae were affected by concentrations 

ranging from 10 to 300 ~g/L (Table 4). Blue-green algae ap~ear to be much 

more resistant to selenium(VI) with 10,000 ~g/L being the lowest 

con~entration repcirted·to affect growth. Kumar (1964) found that a blue-green 

alga developed and lost resistance to sel~nium(VI). The difference in the 

sensitivities of g!een and blue-green algae to selenium(VI) ~ight be of 

ecological significance, particularly in bodies of water susceptible to 

nuisance algal blooms. For example, Patrick et al. (1975) reported that a 

concentration of 1,000 ~g/L caused a natural assemblage of algae to shift 

to a community dominated by blue-green algae. 

At 10,000 ~g/L, ' selenium(VI) is lethal to four species of saltwater 

phytoplankton and lower concentrations increase or decrease growth (Table 6). 

Concentrations as low as 10 ~g/L reduced growth of Porphyridium cruentum 

(Wheeler et al. 1982). 

Although selenium(IV) appears to be more acutely and chronically toxic 

than selenium(VI) to most aquatic animals, this does not seem to be true for 

19 
aquatic plants. Selenium(IV) and selenium(VI) are about equally toxic to the 

freshwater algae Anabaena cylindrica, Anabaena variabilis, Anacystis nidulans, 

and Scenedesmus dimorphus (Kumar and Prakash 1971; Moede et al. 1980). The 

two oxidation states equally stimulated growth of Chrysochromulina 

breviturrita (Wehr and Brown 1985.) On the other hand, selenium(VI) is more 

toxic than selenium (IV) to the freshwater Selenastrum capricornutum (Richter 

1982) and the saltwater Chorella sp. and Platymonas subcordiformis (Wheeler et 

al. 1982). In addition, Fries (1982) found that growth of thalli of the brown 

macroalga, Fucus spiralis, was stimulated more by exposure to selenium(IV) at 

2.605 ~g/L than to the same concentration of selenium(VI). 

A Final Plant Value, as defined in the Guidelines, cannot be obtained 

because no test in which the concentrations of selenium(IV) or selenium(VI) 

were measured and the endpoint was biologically important has been conducted 

with an important aquatic plant species. 

Bioaccumulation 

Selenium( IV) 

Bioconcentration factors (BCFs) for selenium(IV) that have been obtained 

with freshwater species range from 2 for the muscle of rainbow trout to 452 

for the bluegill (Table 5). Adams (1976) studied both uptake and elimination 

of selenium-75 by fathead minnows at average concentrations of 12, 24, and 

50 ~g/L. He found that concentrations in whole fish and in individual 

tissues increased at a rapid rate during the first eight days and at a slower 

rate for the next 88 days. Steady-state was approached, but not reached, in 

96 days. The highest concentrations were found in viscera, possibly due to 

uptake of selenium adhering to food. Elimination of selenium was curvilinear 

and became asymptotic with the time axis after 96 days. Elimination was most 

20 
rapid from the viscera with a half-life of 5.1 days, but the half-life of 

selenium in other tissues was greater than 50 days. 

Adams {1976) also conducted uptake studies with rainbow trout exposed for 

48 days to selenium(IV) at concentrations ranging from 310 to 950 pg/L. 

Some of the trout died, and concentrations were somewhat higher in dead fish 

than in survivors. As with the fathead minnow, the viscera contained more 

selenium than gill or muscle. Based on his tests with the two species, Adams 

(1976) concluded that there was an inverse relationship between BCF and the 

concentration of selenium(IV) in water. 

Hodson et al. (1980) exposed rainbow trout to selenium(IV) from 

fertilization until 44 weeks posthatch. At 53 pg/L in the water the BCF 

ranged from 6 for whole body to 240 for liver. They concluded that selenium 

' in tissues did not increase in proportion to selenium(lV) in water. 

Barrows et al. (1980) exposed bluegills to selenious acid for 28 days. 

They reported a maximum BCF in the whole f·ish of 20 and a half-life of between 

one and seven days. If bluegills bioconcentrate selenium in"the same manner 

as the rainbow trout used by Adams (1976), the 26-day exposure might not have 

been long enough to reach steady-state. 

Lemly (1982) exposed bluegills and largemouth bass to 10 pg/L for 120 

days to determine the effect of hardness and temperature on uptake and 

elimination. For bluegills, the geometric mean whole-body BCF at 20° and 

30°C was 452. For largemouth bass in similar tests, the BCF was 295. For 

both species, the spleen, liver, kidney, and heart had higher concentrations 

than the whole body. Neither water temperature nor hardness had a significant 

effect on concentrations in tissue after 90 days, although earlier values were 

influenced. After 30 days in clean water, selenium concentrations remained 

unchanged in spleen, liver, kidney, and white muscle, but the half-life for 

selenium in gills and erythrocytes was less than 15 days. 

21 
Steady-state BCFs with two saltwater species ranged from 2.88 in chela 

muscle of adult shore crab, Carcinus maenas (Bjerregaard 1982,1985) to 200 in 

whole adult euphausiids, Meganyctiphanes norvegica (Fowler and Benayoun 

1976c). Selenium was accumulated to a higher concentration in gill than in 

hepatopancreas or muscle of the shore crab during exposure to 250 ~g/L. 

The authors suggested that much of the selenium associated with the gill might 

be sorbed to the gill surface. 

Ingestion of food organisms that had been exposed to selenium(IV) can be 

an important source of exposure of fish to selenium (Hodson and Hilton 1983; 

Sandholm et al. 1973; Turner and Swick 1983). Addition of selenium(IV) to 

food reduced survival of rainbow trout (Goettl and Davies 1978). Rudd and 

Turner(1983a,b) found that the bioaccumulation of selenium by fish was reduced 

by sediment and by increased primary productivity. Fowler and Benayoun (1976) 

reported that the BAF for selenium(IV) from food plus water was four times 

higher for an euphausiid than the BCF (uptake from water alone). The blue 

mussel, Mytilus edulis, accumulated selenium at a slow rate when exposed to 

selenium(IV), but did not accumulate selenium when exposed to bis(2-carboxybenzyl)selenium (Pelletier 1986a). 

Selenium{VI) 

Bertram and Brooks (1986) exposed adult fathead minnows to sodium selenate 

in water, in food, and in food and water together. The food was specially 

~ 

prepared by raising algae in a medium containing selenium(VI), feeding the 

algae to daphnids, mixing the exposed daphnids with unexposed daphnids, 

dewatering to form a ncaken, and freezing. Uptake of selenium(VI) from only 

water reached steady-state within 28 days. The whole-body BCFs ranged from 21 

to 52 and decreased as the concentration in water increased (Table 5). Uptake 

of selenium(VI) from food alone or from food and water together did not reach 

22 
steady-state in eight and eleven weeks, respectively. Uptake from food and 

water were additive. 

When juvenile striped bass were exposed in salt water for 60 days to 

selenium(VI) at concentrations of 90 and 1,290 ~g/L, the whole-body 

concentrations were within a factor of two of the concentrations in control 

fish (Klauda 1985). 

Selenium(IV) was bioconcentrated more than selenium(VI) by saltwater 

phytoplankton communities (Wrench and Measures 1982), a freshwater duckweed 

(Bulter and Peterson 1967), and two saltwater invertebrates (Fowler and 

Benayoun 1976a). 

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

tissue, as defined in the Guidelines, is available for selenium and, 

therefore, no Final Residue Value can be calculated. 

Other Data 

Selenium( IV) 

Additional data on the lethal and sublethal effects ~f selenium on 

aquatic species are presented in Table 6. Bringmann and Kuhn (1959a,b,1976, 

1977a,1979,1980b,1981), Jakubczak et al. (1981), and Patrick et al. (1975) 

reported the concentrations of selenium(IV) that caused incipient inhibition 

(defined variously, such as the concentration resulting in a 3% reduction in 

' growth) for algae, bacteria, and protozoans (Table 6). Although incipient 

inhibition might be statistically significant, its ecological importance is 

unknown. Jones and Stadtman (1977) reported stimulation of growth of an 

anaerobic bacterium exposed to 49 ~g/L. Selenium(IV) at a concentration of 

100 ~g/L did not affect crustacean communities in enclosures in a lake 

contaminated by mercury (Saiki et al. 1985). 

23 
Short and Wilber (1980) reported that the calcium balance· in the 

crayfish, Orconectes immunis, was altered by a 30-day exposure to a selenium 

concentration of 10 ~g/L. Hodson et al. (1980) found delayed mortality 

during a 4-day period following cessation of exposure to selenium(IV). Hilton 

et al. (1982) studied the uptake from food, distribution, and elimination of 

selenium(IV) by rainbow trout. Mancini (1983) calculated detoxification rates 

for selenium in various fishes. 

Selenium(VI) 

Dunbar et al. (1983) exposed fed Q. magna to selenium(VI) for seven days 

and obtained an LC50 of 1,870 ~g/L. This value is in the range of the 

48-hr EC50s in Table 1. 

Watenpaugh and Beitinger (1985a) found that fathead minnows did not avoid 

11,200 ~g/L during 30-minute exposures (Table 6). These authors also 

reported (1985b) a 24-hr LC50 of 82,000 ~g/L for the same species and they 

round (1985c) that the thermal tolerance of the species was reduced by 

22,200 ~g/L. Bennett et al. (1986) raised rotifers on algae that had been 

exp~sed to selenium(VI). Fathead minnow larvae that were fed the contaminated 

rotifers weighed less than larvae that were fed control rotifers. Westerman 

and Birge (1978) exposed channel catfish embryos and newly hatched fry for 8.5 

to 9 days to an unspecified concentration of selenium(VI). Albinism was 

observed in 12.1 to 36.97. of the fry during the five years of such exposures. 

The respiratory rate of the eastern oyster, Crassostrea virginica, was 

unaffected by exposure to selenium(VI) at 400 ~g/L for 14 days (Fowler et 

al. 1981). Embryos of the striped bass were quite resistant to selenium(Vl) 

in dilute salt water (Klauda 1985). There was a 937. successful hatch of 

embryos at 200,000 ~g/L, but 507. of 72-day-old juveniles died after four 

days at 87,000 ~g/L. Exposure of juvenile fish for up to 65 days to 

24 
concentrations of selenium(VI) between 39 and 1,360 pg/L caused 

developmental anomalies and pathological lesions. 

Field Studies 

Studies on Belews Lake in North Carolina (e.g., Cumbie as quoted in 

Hodson et al. 1984; Cumbie and Van Horn 1978; Finley 1985; Lemly 1985a,b; 

Sorensen et al. 1984) and Hyco and Catfish Reservoirs in North Carolina 

(Baumann and Gillespie 1986; Gillespie and Baumann 1986; Sager and Cofield 

1984) ·suggest that selenium might be more toxic to certain species of 

freshwater fish than has been observed in chronic toxicity tests. Other 

bodies of water in which the effects of selenium on aquatic organisms have 

been studied include a farm pond in New York (Furr et al. 1979; Gutenmann et 

al. 1976), various lakes and reservoirs in Colorado and Wyoming (Birkner 1978; 

Kaiser et al. 1979), a drainage system in South Carolina (Cherry and Guthrie 

1978; Cherry et al. 1976,1979a,b,1984; Guthrie and Cherry 1976,1979), Martin· 

Creek Reservoir in Texas (Garrett and Inman 1984; Sorensen and Bauer 1984a,b; 

Sorenson et al. 1982), and Kesterson Reservoir in Californi~ (Burton et al. 

1987; Ohlendorf et al. 1986a,b; Saiki 1986a,b). 

Such studies, however, have provided circumstantial, rather than 

definitive, data on the effects of selenium on aquatic life for two major 

reasons: 

1. Few, if any, data are available concerning the oxidation state of 

selenium in the water. Because there are, as yet, no data to show that 

selenium(IV) and selenium(VI) are toxicologically or ecologically 

equivalent, it is difficult to interpret the results of field studies 

that do not use analytical methods (e.g., Oppenheimer et al. 1984; 

Robberecht and Van Grieken 1982; Uchida et al. 1980) that can separately 

25 
measure selenium(IV) and selenium(VI). On the other hand, it is likely 

that most ambient waters contain substantial concentrations of two or 

more oxidation states of selenium (see item 3 on page 2). 

2. Unless the investigator controls the addition of the test material, 

rarely can a field study conclusively pinpoint the cause of any observed 

effects, because it is possible that the effects were caused by a 

combination of agents or by an unmeasured agent. However, if 

circumstantjal evidence from a number of dissimilar situations points in 

the same direction, the inference becomes stronger. 

In spite of the limitations of the available results of field studies, they do 

raise such important questions as: 

a. What are the highest concentrations in water of selenium(-11), 

selenium(IV), selenium(VI), and their combinations that do not 

unacceptably reduce reproduction, and survival of the resulting young, of 

sensitive wa·rmwater fishes? 

b. What are the relative toxicities of seleniumt-II), selenium(IV), 

selenium(VI), and their combinations in food and in water and are the two 

sources additive? 

c. Are selenium(-11), selenium(IV), and selenium(VI) toxicologically or 

ecologically equivalent in aquatic ecosystems? 

Such questions are important and can be answered with properly designed field 

and laboratory studies. 

The severe effects that were observed on the fish community in Belews 

Lake have been attributed, with differing degrees of certainty by various 

authors, to the 10 ~g selenium/L in the lake. Although selenium is 

certainly a good candidate for the cause of the observed effects, studies on 

Belews Lake cannot establish a cause-effect relationship because a variety of 

26 
other inorganic and organic materials undoubtedly entered the lake with the 

selenium. Studies on other bodies of water that contain selenium at 

concentrations in the range of 1 to 30 ~g/L could help confirm or refute 

the theory that selenium is the primary cause of the effects observed in 

Belews Lake, especially if the selenium in the other bodies of water did not 

come from fly ash. 

Several laboratory studies have attempted to confirm that selenium 

affected the fish community in Belews Lake. For example, Lemly (1982) exposed 

bluegills and largemouth bass to selenium(IV) at a concentration of 10 ~g/L 

for 120 days. No mortality occurred in the test, whereas bluegills stocked 

into Belews Lake died in 3 to 4 months when kept in cages and died almost 

immediately when released into the lake (Cumbie as quoted in Hodson et al. 

1984). 

In a novel experiment, Gillespie and Baumann (1986) mated male and female 

bluegills from Hyco Reservoir, which contained a high concentration of 

selenium:·with bluegills from Roxboro City Lake, which contained very little 

selenium. The young survived when females from Roxboro City Lake were mated 

with males from either source. When females from Hyco Reservoir were mated 

with males from either source, the young hatched but died before attaining the 

swim-up stage. The young that died also contained high concentrations of 

selenium, which they must have received from their mothers. It is, of course, 

possible that the young also received one or more toxicants in addition to 

selenium from their mothers because Hyco Reservoir is a cooling reservoir for 

a coal-fired electric power plant. 

For 44 days Finley (1985) fed mayfly nymphs obtained from Belews Lake to 

four bluegills and fed cultured mealworms to four other bluegills. The nymphs 

contained 13.6 ~g selenium/g (wet weight). The four fish fed mealworms 

27 
appeared healthy throughout the test, whereas three of the four fish fed the 

nymphs died. It is possible that bluegills were affected by Finley (1985) but 

not Lemly (1982) because the nymphs also contained one or more toxicants in 

addition to selenium, because the nymphs provided proportionately more 

selenium, or because the nymphs contained a more toxic form of selenium. 

Several feeding studies have shown that aquatic species can be adversely 

affected by consuming food that contains 10 to 13 ~g selenium/g. Thus 

these studies support the idea that. the effects observed by Finley (1985) were 

caused by selenium. In two 42-week feeding studies, mortality of rainbow 

trout increased when their food contained selenium(IV) at a concentration of 

9 ~g/g (Goettl and Davies 1978). Hilton et al. (1980) reported that when 

rainbow trout were fed a food containing selenium(IV) at a concentration of 

13 ~g/g for twenty weeks, growth decreased and mortality increased. Hilton 

and Hodson (1983) obtained similar effects when trout consumed food containing 

11 to 12 ~g/g for sitteen weeks. In· a fourth feeding study with rainbow 

trout, selenium(IV) at 11.4 ~g/g (on a freeze-dried basis) reduced g~owth 

and increased mortality in a sixteen-week test (Hicks et al. 1984). 

Although their tests on early life stages and smoltification of chinook 

salmon were possibly confounded by the presence of other pollutants, the 

results reported by Hamilton et al. (1986) support the results of other 

investigators that concentrations greater than 13 ~g/g (reportedly as 

organoselenium) in food will unacceptably affect salmonids. 

Heinz et al. (1987) fed adult mallards and their ducklings feed that 

contained selenium(IV) or selenomethionine. The number of 21-day old 

ducklings per hen was 9.7 for the controls and 2.0 for the animals that 

received food containing 10 ~g selenium/g as selenomethionine. The 

treatments receiving 10 and 25 ~g/g as selenium(IV) produced 8.1 and 0.2 

28 
ducklings per hen, respectively. Food containing 10 ~g selenium/gas 

selenomethionine resulted in nearly ten times as much selenium in eggs as did 

food containinc 10 ~g/g as selenium(IV). Selenomethionine resulted in more 

selenium in egg white than yolk, but the opposite was true with selenium( IV). 

These data tndicate that rainbow trout, chinook salmon, and mallard ducks 

were affected when they consumed food that contained selenium in the range of 

10 to 13 ~g/g. Most of these studies were conducted by adding selenium( IV) 

to food, but it is likely that at least some of the selenium accumulated in 

food chain organisms would be in a more toxic form. These studies strongly 

indicate that the effects observed by Finley (1985) were indeed caused by 

selenium and that the 10 ~g/L in Belews Lake caused the effects observed 

there. The concentration of selenium in an unaffected upper arm of Belews 

Lake was near or below the detection limit of 5 ~g/L (North Carolina 

Department of Natural Resources and Community Development 1986). 

The freshwater Criterion Continuous Concentration {CCC) should be between 

10 ~g/L and the concentration in the unaffected portion of Belews Lake, 

which is near or below 5 ~g/L. Therefore, the CCC will be set at 

5.0 ~g/L. Eight of the nine Acute-Chronic Ratios in Table 3 are between 

2.651 and 16.26, with a geometric means of 7.993. If the Final Acute-Chronic 

Ratio is assumed to be 7.993, the Final Acute Value would be 39.96 ~g/L, 

and the Criterion Maximum Concentration would be 19.98 ~g/L. 

Unused Data 

Some data on the effects of selenium on aquatic organisms were not used 

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

America {e.g., Asanullah and Brand 1985; Asanullah and Palmer 1980; Fowler and 

Benayoun 1976a,b; Gotsis 1982; Hiraoka et al. 1985; Juhnke and Ludemann 1978; 

29 
Niimi and LaHam 1975,1976; Ringdal and Julshamn 1985; Shultz and Ito 1979; 

Srivastava and Tyagi 1983/1984; Wrench 1978). Results (e.g., Okasako and 

Siegel 1980) of tests conducted with brine shrimp, Artemia sp., were not used 

because these species are from a unique saltwater environment. Adams and 

Johnson (1981), Biddinger and Gloss (1984), Brooks (1984), Chapman et al. 

(1968), Davies (1978), Eisler (1985), Hall and Burton (1982), Hodson and 

Hilton (1983), Hodson et al. (1984), Jenkins (1980), Kay (1984), LeBlanc 

(1984), McKee and Wolf (1963), National Research CounciJ (1976), North 

Carolina Department of Natural Resources and Community Development (1986), 

Phillips and Russo (1978), Thompson et al. (1972), and Versar (1975) compiled 

data from other sources. 

Greenberg and Kopec (1986) and Hutchinson and Stokes (1975) did not 

specify the oxidation state of the selenium used in their tests. Data were 

not used when selenium was a component of an effluent, fly ash, formulation, 

mixture, sediment, or sludge (e.g., Burton et al. 1983; ·Fava et al. 1985; Hall 

et al. 1984; Hamilton et al. 1986; Hildebrand et al. 1976; Jay and Muncy 1979; 

MacFarlane et al. 1986; Phillips and Gregory 1980; Ryther ei al. 1979; Seelye 

et al. 1982; Specht et al. 1984; Thomas et al. 1980b; Wong et al. 1982) 

unless data were available to show that the toxicity was the same as for 

selenium alone. 

Braddon (1982), Christensen and Tucker (1976), Freeman and Sangalang ., (1977), and Olson and Christensen (1980) exposed enzymes, excised tissue, or 

tissue extracts. Results were not used when the test procedures, test 

material, or results were not adequately described (e.g., Bovee 1978; 

Gissel-Nielsen and Gissel-Nielsen 1973,1978; Greenberg and Kopec 1986; Nassos 

et al. 1980). Kaiser (1980) calculated the toxicities of selenium(IV) and 

selenium(VI) to Daphnia magna based on physiochemical parameters. Kumar 

30 
(1964) did not include a control treatment in the toxicity tests. The 

daphnids were probably stressed by crowding in the tests reported by Schultz 

et al. (1980). Siebers and Ehlers (1979) exposed too few test organisms, as 

did Owsley (1984) in some tests. Data were not used when the organisms were 

exposed to selenium by gavage or injection (Hilton et al. 1982; Kleinow 1984; 

Kleinow and Brooks 1986a,b; Sheline and Schmidt-Nielson 1977). 

BCFs and BAFs from laboratory tests were not used when the tests were 

static or when the concentration of selenium in the test solution was not 

adequately measured or varied too much, (e.g., Nassos et al. 1980; Sharma and 

Davis 1980). Reports of the concentrations of selenium in wild aquatic 

organisms (e.g., Baumann and Gillespie 1986; Baumann and May 1984; Brezina and 

Arnold 1977; Birkner 1978; Cappon 1984; Cappon and Smith 1981, 1982a,b; Cumbie 

and Van Horn 1978; Davoren 1986; Fowler et al. 1975; Froslie et al. 1985; 

Gillespie and Baumann 1986; Greig and J~nes 1976; Heit and Klusek 1985; Heit 

et al. 1980; Johnson 1987; Kaiser et al. 1979; Lemly 1985a; Lowe et al. 1985; 

Lucas et al. 1970; Lytle· and Lytle 1982; May and McKinney 1981; Mehrle et al. 

1982; Moharram et al. 1987; Ohlendorf et al. 1986a,b,c; Okazaki and Panietz 

1981; Pakkala et al. 1972; Payer and Runkel 1978; Payer et al. 1976; 

Pennington et al. 1982; Sager and Cofield 1984; Saiki 1986a,b; Shultz and Ito 

1979; Seelye et al. 1982;· Sorensen and Bauer 1984a,b; Sorensen et al. 

1982,1983,1984; Speyer 1980; Uthe and Bligh 1971; Walsh et al. 1977; Weber 

1985; Winger and Andreasen 1985; Winger et al. 1984; Woock and Summers 1984; 

Zatta et al. 1985) were not used to calculate BAFs when either the number of 

measurements of the concentration in water was too small or the range of the 

measured concentrations was too large. 

31 
Summary 

Selenium( IV) 

Acute values for 23 freshwater fish and invertebrate species in 22 genera 

range from 340 ~g/L for the amphipod, Hvalella azteca, to 203,000 ~g/L 

for the leech, Nephelopsis obscura. Although twelve of the twenty-three 

species are fishes, both the two most sensitive and the two most resistant 

species are invertebrates. Chronic values are available for two fishes and 

two invertebrates and range from >47 to 692 ~g/L. ·In a separate test, a 

90-day LC50 of 54 ~g/L was obtained with rainbow trout. The acute-chronic 

ratios for the acutely more sensitive species range from 5.6 to 13.3. 

Toxicity values for nine species of freshwater algae range from 500 to 

30,000 ~g/L. Uptake of selenium(IV) by fish takes about 100 days to reach 

steady-state and bioconcentration factors from 2 to 452 have been reported. 

Acute toxicity values are available for 16 species of saltwater animals, 

including 8 invertebrates and 8 fishes, and range from 599 #g/L for larvae 

of the haddock, Melanogrammus aeglefinus, to 17,350 ~g/L for adults of the 

fourspine stickleback, Apeltes guadracus. Fish and invertebrates have similar 

ranges of sensitivities, and the acute values for the seven most sensitive 

species differ only by a factor of 3.2. There was no consistent relationship 

between life stage of invertebrates or fish and their insensitivity to 

selenium( IV). 

Chronic toxicity data are available for two saltwater animals, the mysid, 

Mysidopsis bahia, and the sheepshead minnow, Cyprinodon variegatus. The 

chronic values and the acute-chronic ratios are 211.7 ~g/L and 7.085 for 

the mysid, and 675.2 ~g/L and 10.96 for the sheepshead minnow. At a 

concentration of 7,930 ~g/L, selenium(IV) caused a 50% reduction in 

chlorophyll a in a test with the saltwater diatom, Skeletonema costatum, but 

32 
growth of three species of algae was stimulated by concentrations of 10 to 

10,000 ~g/L. The steady-state bioconcentration factors for two saltwater 

species range from 3.88 in chela muscle of adult shore crabs, Carcinus maenas, 

to 200 in whole adult euphausiids, Meganyctiphanes norvegica. 

Selenium(Vl) 

The acute toxicity of selenium(VI) has been determined with twelve 

freshwater animal species. The acute values range from 75 ~g/L with the 

amphipod, Gammarus pseudolimnaeus, to 442,000 ~g/L with the leech, 

Nephelopsis obscura. Chronic toxicity tests have been conducted with Daphnia 

magna, the fathead minnow, and the rainbow trout. The chronic values range 

from 565.5 to 1,999 ~g/L. and the acute-chronic ratios range from 2.651 to 

16.26. Selenium(Vl) affected nine·algal species at concentrations ranging 

from 10 to 39,000 ~g/L. Bioaccumulation factors obtained with the fathead 

minnow ranged from 21 to 52 ~g/L. 

Few data are available concerning the effects of.selenium(VI) on 

saltwater species. Acute toxicity tests with prolarvae and juveniles of 

striped bass, Marone saxatilis, resulted in 96-hr LC50s of 9,790 and 

85,840 ~g/L, respectively. No chronic tests have been conducted on 

selenium(Vl) with saltwater animals. The growth of an alga was increased by 

10 ~g/L. Steady-state bioconcentration factors of 1 to 16 were obtained 

with juvenile striped bass. 

Other 

For ten of the eleven freshwater and saltwater fish and invertebrate 

species for which comparable acute data are available, selenium(IV) is 1.6 to 

3.6 times more toxic than selenium(VI). For the eleventh species, 

selenium{IV) is 57 times less toxic. Chronic toxicity tests have been 

conducted on both selenium{IV) and selenium(VI) with three freshwater species 

33 
and no saltwater species. For all three animals selenium(IV) was 5 to 32 

times more toxic than selenium(VI). Eight of the nine acute-chronic ratios 

available for the two oxidation states are between 2.6 and 17; the ninth ratio 

is 141.5 and was obtained with an acutely resistant species. In contrast to 

the data obtained with aquatic animals, selenium(VI) is either as toxic as or 

more toxic than selenium(IV) to aquatic plants. Selenium(IV) seems to be 

bioconcentrated more than selenium(VI) by aquatic plants and animals. 

Salmonids and mallard ducks were severely affected when they con~umed 

food that contained selenium at concentrations of 10 to 13 ~g/g. It is 

likely that the populations of several species of warmwater fishes were 

destroyed by selenium at a concentration of 10 ~g/L in Belews Lake. 

National Criteria 

The procedures described in the "Guidelines for Deriving Numerical 

National Wat~r Quality Cri~eria· for the Protection of Aquatic Organisms and 

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

is very sensitive, freshwater aquatic organisms and their uses should not be 

affected unacceptably if the four-day average concentration of selenium does 

not exceed 5.0 ~g/L more than once every three years on the average and if 

the one-hour average concentration does not exceed 20 ~g/L more than once 

every three years on the average. 

The procedures described in the ''Guidelines for Deriving Numerical 

National Water Quality Criteria for the Protection of Aquatic Organisms and 

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

is very sensitive, saltwater aquatic organisms and their uses should not be 

affected unacceptably if the four-day average concentration of selenium does 

not exceed 71 ~g/L more than once every three years on the average and if 

34 
the one-hour average concentration does not exceed 300 ~g/L more than once 

every three years on the average. If selenium is as toxic to saltwater fishes 

in the field as it is to freshwater fishes in the field, the status of the 

fish community should be monitored whenever the concentration of selenium 

exceeds 5.0 ~g/L in salt water. 

Implementation 

Because of the variety of forms of selenium in ambient water and the lack . of de(initive information about their relative toxicities to aquatic species, 

no available analytical measurement is known to be ideal for expressing 

aquatic life criteria for selenium. Previous aquatic life criteria for metals 

and metalloids (U.S. EPA 1980b) were expressed in terms of the total 

recoverable measurement (U.S. EPA 1983a), but newer criteria for metals and 

metalloids have been expressed in terms of the acid-soluble measurement 

(1985b). Acid-soluble selenium (operationally defined as the selenium that 

passes through a 0.45 ~m membrane filter after the sample has been 

acidified to a pH between 1.5 and 2.0 with nitric acid) is ~robably the best 

measurement at the present for the following reasons: 

1. This measurement is compatible with nearly all available data concerning 

toxicity of selenium to, and bioaccumulation of selenium by, 

aquatic organisms. It is expected that the results of tests used in the 

derivation of the criteria would not have changed substantially if they 

had been reported in terms of acid-soluble selenium. 

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

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

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

additi~n. this measurement probably will not measure several forms, such 

35 
as selenium 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. 

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

used to express criteria is likely to be used to measure selenium in 

aqueous effluents. Measurement of acid-soluble selenium is expected to 

be applicable to effluents. If desired, dilution of effluent with 

receiving water before measurement of acid-soluble selenium might be used 

to determine whether the receiving water can decrease the concentration 

of acid-soluble selenium because of sorption. 

4. The acid-soluble measurement is expected to be useful for most metals and 

metalloids, thus minimizing the number of samples and procedures that are 

necessary. 

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

the time of coll~ction, as.does the diss~lved.measurement. 

!. For the measurement of total acid-soluble selenium the only treatment 

required at the time of collection is preservation by acidification to a 

pH between 1.5 and 2.0, similar to that required for the total 

recoverable measurement. 

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

of most samples of ambient water probably will not substantially affect 

the result of the measurement of total acid-soluble selenium. However, 

acidification might not prevent oxidation or reduction of selenium(-11}, 

selenium(VI), or selenium(IV) (May and Kane 1984). Therefore, 

measurement of acid-soluble selenium(IV) and/or acid-soluble 

selenium(VI) might require separation or measurement at the time of 

collection of the sample or special preservation to prevent conversion of 

one oxidation state of selenium to the other. 

36 
8. Ambient waters have much higher buffer intensities at a pH between 1.5 

and 2.0 than they do at a pH between 4 and 9 (Stumm and Morgan 1981) 

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

the result substantially. 

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 

acid-soluble selenium, the analysis for total acid-soluble selenium can 

be performed using either furnace or hydride atomic absorption 

spectrophotometric or ICP-atomic emission spectrometric analysis (U.S. 

EPA 1983a), as with the total recoverable measurement. It might be 

possible to separately measure acid-soluble selenium(IV) and acid-soluble 

selenium(VI) using the methods described by Oppenheimer et al. (1984), 

Robberecht and Van.Grieken (1982), and Uchida et al. (1980). 

Thus, expressing aquatic life criteria for selenium in terms of the 

acid-soluble measurement has both toxicological and practical advantages. The 

U.S. EPA is considering development and approval of a method for a measurement 

such as acid-soluble. 

Metals and metalloids might be measured using the total recoverable 

method (U.S. EPA 1983a). This would have two major impacts because this 

method includes a digestion procedure. First, certain species of some metals 

and metalloids cannot be measured because the total recoverable method cannot 

distinguish between individual oxidation states. Second, in some cases these 

criteria would be overly protective when based on the total recoverable method 

because the digestion procedure will dissolve selenium that is not toxic and 

cannot be converted to a toxic form under natural conditions. Because no 

measurement is known to be ideal for expressing aquatic life criteria for 

37 
selenium or for measuring selenium in ambient water or aqueous effluents, 

measurement of both acid-soluble selenium and total recoverable selenium in 

ambient water or effluent or both might be useful. For example, there might 

be cause for concern when total recoverable selenium is much above an 

applicable limit, even though acid-soluble selenium is below the limit. 

In addition, metals and metalloids might be measured using the dissolved 

method, but this would also have several impacts. First, whatever analytical 

method is specified for measuring selenium in ambient surface water will 

probably also be used to monitor effluents. If effluents are monitored by 

measuring only the dissolved metals and metalloids, the effluents might 

contain some selenium that would not be measured but might dissolve, due to 

dilution or change in pH or both, when the effluent is mixed with receiving 

water. Second, measurement of dissolved selenium requires filtration of the 

sample at the time of collection. Third, the dissolved measurement is 

.especially inappropriate for use with such metals as aluminum that can exist 

as hydroxide and carbonate precipitates in toxicity tests and in effluents. 

Use of different methods for different metals and metalloids would be 

unnecessarily complicated. For these reasons, it is recommended that aquatic 

life criteria for selenium not be expressed as dissolved selenium. 

As discussed in the Water Quality Standards Regulation (U.S. EPA 1983b) 

and the Foreword to this document, a water quality criterion for aquatic life 

has regulatory impact only after it has been adopted in a State water quality 

standard. Such a standard specifies a criterion for a pollutant that is 

consistent with a particular designated use. With the concurrence of the U.S. 

EPA, States designate one or more uses for each body of water or segment 

thereof and adopt criteria that are consistent with the use(s) (U.S.EPA 

38 
1983c,1987). In each standard a State may adopt the national ~riterion, if 

one exists, or, if adequately justified, a site-specific criterion. 

Site-specific criteria may include not only site-specific criterion 

concentrations (U.S. EPA 1983c), but also site-specific, and possibly 

pollutant-specific, durations of averaging periods and frequencies of allowed 

excursions (U.S. EPA 1985c). The averaging periods of "one hour" and "four 

days" were selected by the U.S. EPA on the basis of data concerning how 

rapidly some aquatic species react to increases in the concentrations of some 

pollutants, and "three years" is the Agency's best scientific judgment of the 

average amount of time aquatic ecosystems should be provided between 

excursions (Stephan et al. 1985; U.S. EPA 1985c). However, various species 

and ecosystems react and recover at greatly differing rates. Therefore, if 

adequate justification is provided, site-specific and/or pollutant-specific 

concentrations, durations, and frequencies may be higher or lower than those . . 

given in national water quality criteri~ for aquatic life. 

Use of criteria, which have been adopted in State water quality 

standards, for developing water quality-based permit limits and for designing 

waste treatment facilities requires selection of an appropriate wasteload 

allocation model. Although dynamic models are preferred for the application 

of these criteria (U.S. EPA 1985c), limited data or other considerations might 

require the use of a steady-state model (U.S. EPA 1986). Guidance on mixing 

zones and the design of monitoring programs is also available (U.S. EPA 1985c, 

1987) . 

39 
Table I. Acute Toxicity or Seleniu• to Aquatic Ani•als 

Hard1ess LC50 Species Ueu 

(•g/L as ar £C50 Acute. Value 

Species Method a Che•ical .£!!!!JL (ug/L)b (ug/L) Rererence 

rR£SHWAT£R SP£CI£S 

Seleniu•(IV) 

Hydra ( odul t), s. .. Sodium I, 700 I, 700 Brooke et al. 1985 

Hydra sp. selenite 

Leech ( odul t). S, .. Sodium 49 8 203,000 203,000 Brooke et al. 1985 

Nephelopsis obscuro selenite 

Sno i I (adult). s. .. Sodium 50.6 53,000 Brooke et al. 1985 

~ hypnorum selenite 

Sno i I {adult), s ... Sodium 49.8 23,000 34,910 Brooke et ol. 1985 

Aplexa hypnorum selenite ~ 

0 

Sna i I , s. u Sodium 45.7 24,100 24,100 Reading 1979 

Physo sp. selenite 

Cladoceron (<24hr), s. u Sodium I 00. 8. 600 Owsley 1984; Ows I ey 

Ceriodophnio offinis selenite and NcCouley 1986 

Clodoceron (36-60hr), s. u Sodium I 00.8 720 Ows I ey 1984 

Ceriodophnio offinis selenite 

'. 

Clodoceron (84-1 08 hr). s. u Sodium I 00. & 640 Owsley 1984 

Ceriodophnio offinis selenite 

Clodoceron (72-120 hr), s. u Sodium 100.8 '480 ( 603. 6 Ows I ey 1984 

Ceriodo11hnio offinis selenite 
Tobie I. (conlinued) 

Horduss LCSO Species Ue11 

(•g/l os or £C50 Acute Valu 

Species Uethod0 Che•ical ~lL b feg/L) feg/L} Rehre11ce 

Clodoceron, s. u Sodium 214 2,500 Bringmonn and Kuhn 

Daphnia mogno selenite 1959o 

Clodoceron, s. u Selenious 72 430 LeBlanc 1980 

Daphnia magna ocidc 

Clodoceron, s. .. Sodium 129.5 1,100 Dunbar et ol. 1983 

Daphnia magna selenite 

Clodoceron, s. .. Sodium 138 450 Boyum 1984 

Daphnia magna selenite 

Cladoceron (<24 hr) , s. u Sodium 215 Adams and Heidolph 

Daphnia magna selenite 1985 

Cladoceron (<24 hr), s. u Sodium 40 870 llayer and [IJersieck 

Daphnia magna selenite 1986 

.!:'-

..... Clodoceran (<24 hr), s. u Sodium 280 2,370 Woyer and [II ers i eck 

Daphnia magna selenite 1986 

Clodoceron, s. .. Selenious 220d I, 220 855.8 Kimball, llonuscript 

Daphnia magna acid 

Clodoceran, s. .. Sodium 46.4 3,870 3,870 Reading 1979; Reading 

Do~hnio .lli.ll selenite and Buikema 198l 

' 
Tobie I. (continued) 

Hord~ess LCSO Species Me .. 

(•g/L" as or £C50 Acute Vat .. 

Species Uetllod0 Che•ical ..!!Q!lL (ug/L)b (ug/L) Refere•ce 

Amphipod (odult), s . .. Sodium 48.3 4,300 Brooke et at. 1985 

Gommorus pseudol imnoeus selenite 

Amphipod (odult), s ... Sodium 53.6 I ,700 2,704 Brooke 1987 

Gommorus pseudolimnoeus selenite 

· Amph i pod, r. .. Sodium 329 340 340 Holter et at. 1980 

Hvolello oztec:o selenite 

Widge, s. u Sodium 39 24,150 Woyer and [llersieck 

Chironomus plumosus selenite 1986 

Widge, s. u Sodium 280 21,850 25,930 Woyer and [llersieck 

Chironomus plumosus selenite 1986 

.1::-

N Widge, r. .. Selenium 48.0 42,500 42,500 Call et ol. 1983 

Tony tarsus dissimilis dioxide 

Rainbow trout, s. u Sodium 330 4,500 Adams 1976 

Solmo goirdneri selenite 

Rainbow trout, S, u Sodium 330 4,200 Adams 1976 

Solmo goirdneri selenite 

Rainbow trout, s. u Sodium 212 I, 800 Hunn et ol. 1987 

Solmo goirdneri selenite 

Rainbow trout, r. .. Sodium 30 12,500 Goettl and Davies 

Salmo goirdneri selenite 1976 

Rainbow trout, r. .. Sodium 135 8,800 I 0, 490 Hodson et a I. 1980 

Solmo gairdneri selenite 
Table I. (continued) 

Har-dness LC50 Species Wean 

(•g/l as or- £C50 Acute-Value 

Species Wetboda Che11ical caco3L (ug/L)b (ug/L) Refer-ence 

Brook trout (odult), r. .. Selenium 157 I 0, 200 10,200 Cardwell et al. 

Salvelinus fontinolis dioKide 1976o,b 

Goldfish, r . .. Selenium 157 26,100 26,100 Cardwell et ol. 

Carossius ourotus dioKide 1976o,b 

Common corp, R, u 35,000 35,000 Sato et ol. 1980 

Cyprinus carpio 

fathead minnow, S, u Sodium 312 I 0, 500 Adams 1976 

Pimepholes promelos selenite (I3°C) 

fathead minnow, s. u Sodium 312 II, 300 Adams 1976 

Pimepholes promelas selenite (I3°C) 

l..oJ "' fathead minnow, s. u Sodium 303 6,000 Adams 1976 

Pimepholes promelos selenite ( 20°C) 

fathead minnow, s. u Sodium 303 7,400 Adams 1976 

Pimephales promelas selenite (20°C) 

fathead minnow, S, u Sodium 292 3,400 Adams 1976 

Pimephales promelas selenite (25°C) 

fathead minnow, S, u Sodium 292 2,200 Adams 1976 

Pimephales promelas Selenite ( 25 ° C) 

fathead minnow (30 days), s' lot Sodium 51. I I, 700 Brooke et a I . 1985 

Pimephales promelas selenite 
Table I. (coni i nued) 

Hardaess LCSO Species Yeaa 

(•g/L as or £CSO Ant~ Value 

Species Yetllod0 Che•ical caco1L b (f!g/L) (eg/L) Refereace 

rot head minnow (juvenile), s. u Sodium 40 7,760 Yoyer and [Jiersieclt 

Pimepholes promelos selenite 1986 

ratheod minnow (fry), r. 

J 

M Selenium 157 2,100 Cardwell et ol. 

Pimepholes promelos dioxide 1976o,b 

rotheod minnow (juvenile), r. .. Selenium 15~ 5,200 Cardwell et ol. 

Pimepholes promelos dio11ide 1976o .. b 

rotheod minnow, r. M, Selenious 220d 620 Kimball, 

Pimephales promelas acid Manuscript 

rothead minnow, r. M Selenious 220d 970 I, 601 Kimball, 

Pimephales promelas acid Manuscript 

~ 

~ White sucker, r. M Sodium I 0. 2 29,000 Kloverkomp et ol. 

Cotostomus commersoni selenite 1983o 

White s uc Iter, r. M Sodium 18 31,400 30,180 Duncan and 

Catostomus commersoni selenite Klaverltomp 1983 

Striped bass ( 63 days}, s. u Sodium 40 I, 325 Polowski et ol. 1985 

Morone soxotilis selenite 

Striped boss ( 63 days). s. u Sodium 285 2,400 I, 783 Polowski et a I . 1985 

Morone soxotilis selenite 

Channel catfish (juvenile), s. .. Sodium 49.8 16,000 Brooke et ol. 1985 

lctalurus eunctatus selenite 
Tobie I. (contiaued) 

Hardaess LCSO Species Meaa 

{•g/L es or £CSO Ante Vehe 

Species Metllod0 Ch-i cal ~lL (f!g/L)b (f!gAI Reference 

Channel catfish (juveni I e), s. u Sodium 41 4,110 Wayer and Ellersieck 

lctalurus punctatus selenite 1986 

Channel catfish, r. il Selenium 157 13,600 13,600 Cardwell et al. 

lctalurus punctatus dioxide 1976a,b 

rlagfish, r. .. Selenium 157 6,500 6,500 Cardwell et a I. 

Jordanella floridae dioxide 1976a,b 

Wosquitofish, S, u Sodium 45.7 12,600 12,600 Reading 1979 

Combusia affinis selenite 

Bluegill (juvenile), S, .. Sodium 50.5 12,000 Brooke et al. 1985 

lepomis macrochirus selenite 

.s:-. 

U1 B I ueg iII , r. .. Selenium 157 28,500 28,500 Cardwell et al. 

lepomis mocrochirus dioxide 1976a,b 

Yellow perch, r. .. Sodium I 0. 2 11. 1ooe II ,700 K I averkomp et ol. 

Perea flovescens selenite 1983o 

Seleni u•(VI} 

Hydro (adult). s' .. Sodium 53.6 7,300 7,300 Brooke et a I . 1985 

Hydra sp. selenate '· 

leech (adult). S, w Sodium 49.3 442,000 442,000 Brooke et o I . 1985 

Nephelopsis obscuro selenate 
Table I. (continued) 

Hardness LCSO Species Ueoa 

(•g/l OS or [CSO Acute Value 

Species Uetllod0 Che•icol Coco3L b (f!g/L) (,g/L) Reference 

Sno i I, s . .. Sodium 51.0 193,000 193,000 Brooke et ol. 1985 

Aplexo hypnorum selenate 

' Clodoceron, s. .. Sodium 129.5 5,300 Dunbar et ol. 1983 

Daphnia magna selenate 

Clodoceron, S, .. Sodium 138 I, 010 Boyum 1984 

Daphnia magna . selenate 

Clodoceron, s. .. Sodium 48.1 570 I, 450 Brooke et ol. 1985 

Daphnia magna selenate 

Cladoceran, S, .. Sodium 138 246 246 Boyum 1984 

Daphnia pulicario selenate 

-!:'-

0\ Amphipod (adult), s. .. Sodium 46. I 75 Brooke et a I. 1985 

Gammarus pseudo I imnaeus sel enote 

Amphipod (adult), S, .. Sodium 51.0 57 65.38 Brooke 1987 

Gommorus pseudo I imnaeus selenate 

Amphipod, f, u Sodium 336.8 760 760 Adams 1976 

Hyolello ozteco selenate 

llidge (3rd instor), s. .. Sodium 49.4 20,000 20,000 Brooke et a I . 1985 

Paratanytarsus selenate 

parthenogeneticus 

Rainbow trout (juvenile), s. .. Sodium 51.0 24,000 Brooke et a I . 1985 

Salmo gairdneri selenate 

Rainbow trout, f. .. Sodium 45 47,000 47,000 Spehar 1986 

Salmo gairdneri selenate 
Table I. ( cont i ned) 

Hardeess LC50 Species Ueu 

(•g/l OS or £CSO Acute Val11e 

Species Uetllod0 ...f.!f!!1L b Che•icol (pg/L} leg/q Aefereace 

rat head minnow, S, u Sodium 323 II ,800 Ad oms 1976 

Pimephales promeles selenate 

' rathead minnow, S, u Sodium 323 II, 000 Adams 1976 

Pimepholes promeles selenate 

rathead minnow, s. u Sodium 323 12,500 Adams 1976 

Pimephales promeles selenate 

ratheod minnow {juvenile), s. .. Sodium 47.9 2,300 Brooke et a I . 1985 

Pimephales promelas selenate 

ratheod minnow, r. .. Sodium 46 5,500 5,500 Spehar 1986 

Pimephales promelas sel enote 

~ 

...... Channel catfish S, .. Sodium 51 .0 66,000 66,000 Brooke et al. 1985 

(juvenile), sel enote 

lctalurus punctotus 

B I ueg iII {juveni I e), s. .. Sodium 50.4 63,000 63,000 Brooke et a I. 1985 

Leeomis mocrochirus selenate 
Tobie I. {continued) 

LCSO Species Men 

Soli1ify or ECSO Ante Vohe 

Species Uetllod 0 Che•icol (g/tg) b (,g/L) ,,,fl) Refere1ce 

SALTWATER SPECIES 

Seleniu•(IV) 

Blue mussel (embryo). s. u Selenium 33.79 >10,000 >10,000 Wort in et ol. 1981 

llytilus edulis oxide 

Pacific oyster {embryo), s. u Selenium 33.79 >10,000 Glickstein 1978; 

Crossostreo ~ oxide llortin et ol. 1981 

Pacific oyster {embryo), s. u Sodi urn 33.79 >10,000 >10,000 Glickstein 1978 

Crossostreo ~ selenite 

Copepod (adult), s, u Selenious 30 2. II 0 2 ,II 0 Lussier 1986 

Acort i o cl ous i acid ~ 

CXl 

Copepod (adult), S, u Selenious 30 839 839 Lussier 1986 

Acartio tonso acid 

llysid (juvenile), s. u Selenious 600 U.S. £PA 1978 

llysidopsis bahia acid 

llysid (juvenile), f . .. Selenious 15-20 I, 500 I, 500 Word et al. 1981 

l,lysidopsis bohio acid 

Brown shrimp (juvenile), S, u Sodium 30 I, 200 I, 200 Ward et al. 19BI 

Penaeus oztecus selenite 

Dungeness crab (zoea I ) , S, u Selenium 33.79 I, 040 I, 040 Glickstein 1978 

Cancer magister oxide 
Tobie I. (continued) 

LCSO Species Wean 

Salinity or £C50 Ante Value 

Species Uethda Che•i col (q/td b l,gll) fug/L} Rererence 

Blue crab (juvenile), s. u Sodium 30 4,600 4,600 Word et al. I 981 

Collinectes sopidus selenite 

Haddock (larva), s. u Selenious 30 599 599 Cord in 1986 

Welanogrommus oeglefinus acid 

Sheepsheod minnow s. u Seleniaus 6,700 Heitmuller et a I. 

(Juvenile), acid 1981 

Cvrinodon variegotus 

Sheepsheod minnow r. w Sodium 30 7,400 7,400 Word et a I. 1981 

{juvenile), selenite 

Cyrinodon voriegotus 

Atlantic silverside s. u Selenious ~ 

30 9,725 9,725 Cardin 1986 

\D {juvenile), acid 

t.lenidio menidia 

fourspine stickleback s. u Selenious 30 17,350 17,350 Cardin 1986 

{adult), acid 

Apeltes guodroc::us 

Striped boss, s. u Sodium I. 550 I, 550 Polowski et a I. 

~ soxatilis selenite 1985 

Pinfish {juvenile), s. u Sodium 30 4,400 4,400 Ward et al 1981 

Lagodon rhomboides selenite 

Summer flounder (embryo), s. u Selenious 30.2 3,497 3,497 Cardin 1986 

Para I i cht hys dentatus acid 
Table I. ( conti aued) 

LCSO Species Ileal 

Sali1ify or £C50 lute Val .. 

Species llethd0 Che•ical (g/kg) (ug/L) b ,,,jq ReFereace 

Winter flounder (larva), s. u Seleniaus 30 14,240 Cardin 1986 

Pseudopleuronectes acid 

american us 

Winter f I ounder (larva), s. u Selenious 28 15,010 14,650 Cardin 1986 

Pseudopleuronectes acid 

americanus 

Sele•i••(VI) 

Striped bass (prolarvae), r.w Sodium 3.5-4.2 9,790 Klauda 1985 

Worone saxatilis selenate 

Striped bass (juvenile), r.w Sodium 6.0-6.5 85,840r 9,790 Klauda 1985 

V1 Worone soxotilis selenate 

0 

aS= Static; R =Renewal; r = rlow-through; W = lleasured, U =Unmeasured. 

b Concentration of selenium, not the chemical. 

c Reported by Borrows et al. (1980) in work performed in the same laboratory under the same contract. 

d rrom Smith et al. (1976). 

e Calculated from regression equation. 

Not used in calculation of Species Wean Acute Value because data.are available for a more sensitive life stage. 
Table 2. Chroaic Toxicity or Seleniu• to Aquatic Ani•als 

Hardness Cllronic 

(•g/L as li•its Cllronic Valu 

Species Test 0 Che•ical .£!9!3L (ug/L)b (fAg/L) Reference 

fR£SHIAT£R SP£CI£S 

Set eni u•ll V) 

Clodoceron, LC Sodium 240-310 II 0-237 161.5 Adams and Heidolph 1985 

Daphnia magna selenite 

Clodoceron, LC Selenious 220c 70-120 91.65 Kimball. Wonuscript 

Daphnia magna acid 

Clodoceron, LC Sodium 46.4 600-800 692.8 Reading 1979; Reading 

Daphnia .P.!!.!..£.!. selenite and Buikema 1983 

Rainbow trout, £LS Sodium 30 60-130 88.32 Goettl and Davies 

Solmo goirdneri selenite I 977 Vl 

- Rainbow trout, [LS Sodium 135 >47d >47 Hodson et at. 1980 

Solmo goirdneri selenite 

fathead minnow, £LS Selenious 220c 83-153 II 2. 7 K imbo II. Wonuscript 

Pimephales promelos oci d 

Seleniu•(VJ) 

Cladoceran, LC Sodium 129.5 I ,730-2,310 I, 999 Dunbar et ol. 

Daphnia magna selenate 1983 

Rainbow trout, [LS Sodium 45 2,200-3,800 2,891 Spehar 1986 

Salmo gairdneri selenate 

fathead minnow, [LS Sodium 45-47 390-820 565.5 Spehar 1986 

Pimeehales eromelas selenate 
\Jl 

N 

Table 2. (co1tined) 

Cllro1ic 

Sol hi ty liai ts Cllroaic Valu 

Species Test• Cheaical {g/tg) ,,,!L) b (flg/L) 

SALTWATER SP£Cl£S 

Sel en i"ua{ IV) -1 

Wysid, LC Selenious 26 140-l2Q. 211.7 

Wysidopsis !.!!.h.l.! acid 

Sheepsheod minnow, ElS Sodium 27 470-970 675.2 

Cyprinodon voriegotus selenite 

0 LC = life-cycle or partial life-cycle; [LS =early life-stage. 

b Weasured concentrations of selenium. 

c rrom Smith et ol. (1976). 

d None of the tested concentrations caused effects that were considered unacceptable. 

Species 

Clodoceron, 

Daphnia magna 

Cladoceron, 

Daphnia .l!..!!.!.ll 

Acute-Chronic Ratio 

Hordness 

(ag/l OS 

Coto3L 

220 

46.4 

Acute Value 

(f1q/L) 

Seleniua(IV) 

I, 220 

3,870 

C.ronic Value 

(f1g/L) 

91.65 

692.8 

13.31 

5.586 

Refereace 

u.s. EPA 1978; Word 

et ol. 1981 

Word et ol. 1981 
Table 2. (continued) 

Hardness 

{•g/l OS Acute Value Chroaic Value 

Species ..!!!23L (ug/L} (ug/L} !ill.! 

Rainbow trout, 30 12,500 88.32 I 41.5 

ll.!.m.2, gairdneri 

Rainbow' trout, 135 8,800 ) 47 <187.2 

Salmo gairdneri 

rathead minnow, 220 775.5a 112.7 6.881 

Pimephales promelas 

Wysid, 26b I, 500 211 . 7 7.085 

Wvsidopsis ~ 

Sheepsheod minnow, 27b 7,400 675.2 I 0. 96 

Cvprinodon variegotus 

VI 

VJ 

Seleah•(VI) 

Cladoceran, 129.5 5,300 I, 999 2. 651 

Daphnia magna 

Rainbow trout, 45 47,000 2,891 16.26 

Salmo gairdneri 

rathead minnow, 45-47 5,500 565.5 9.726 

Pimephales promelas 

a Geometric mean of two values in Table I. 

b Salinity (g/kg), not hardness. 
Table 3. Raakecl Ge•us Yea• Acute Values' wi til Species Wean Acute-CIIra•ic Ratios 

Ge•us Yea• Species Wean Species Weu 

Ante Value Ante Value Ante-CIIro•ic 

Rad 0 (ug/L) Species (ug/L)b Rat ioc 

rRESHWATER SPECIES 

Sele•i••(IV) 

22 203,000 leech, 203,000 

Nephelopsis obs·curo 

21 42,500 Widge, 42,500 

Tony tarsus dissimilis 

20 35,000 Common corp, 35,000 

Cyprinus carpio. 

19 34,910 Snoi I, 34,910 

\J1 Aplexo hypnorum 

J:-

18 30,180 White sucker, 30,180 

Cotostomus commersoni 

17 28,500 81 ueg iII , 28,500 

lepomis macrochirus 

16 26,100 Goldrish, 26 100 

Carossius ourotus 

IS 25,930 Widge, 25,930 

Chironomus plumosus 

14 24, I 00 Sno i I , 24,100 

Physo sp. 
Table l. {continued) 

Ceaus Yean Species Yen Species Meu 

Acute Value Acute Value Acute-Cbo•ic 

Ranta (f1g/L) Species (f1g/Ll b . c Ratio 

ll 13,600 Channel catfish, 13,600 

lctalurus punctatus 

12 12,600 Wosquitofish, 12,600 

Combusia affinis 

II II .700 Yellow perch, II .700 

Perea flovescens 

I 0 I 0, 490 Roi nbow trout, I 0, 490 141.5 

Solmo goirdneri 

9 I 0, 200 Brook trout, I 0, 200 

Solvelinus fontinolis 

\J1 

\J1 8 6,500 Flogfish, 6,500 

Jordonell o floridoe 

7 2,704 Amphipod, 2,704 

Commorus pseudolimnoeus 

6 I, 820 Clodoceron, 855.8 13.31 

Daphnia magna 

Clodoceron, 3,870 5.586 

Daphnia .l!.ll!! 

5 I, 78l Striped boss, I, 78l 

Worone soxotilis 
Table 3. (continued) 

Genus Yean Species Yean Species Yen 

Acute Value Acute Value Acute-CIIruic 

Rank 0 (uq/L) Species (uq/L)b Ratioc 

4 I, 700 Hydra, I, 700 

Hydra sp. 

3 I ,601 Fathead minnow_. I, 601 6.881 

Pimephales pramelas 

2 <603.6 Cladoceran, <603.6 

Ceriadaphnia afrinis 

340 Amphipod, 340 

Hyalella ~ 

Seleniua(VJI 

VI 

0\ II 442,000 Leech, 442,000 

Nephelapsis abscura 

I 0 193,000 Sna i I, 193,000 

Aplexa hypnarum 

9 66,000 Channel catfish. 66,000 

lctalurus purictatus 

8 63,000 Bluegill, 63,000 

Lepomis macrochirus 

7 47,000 Rainbow trout, 47,000 I 6. 26 

Salmo gairdneri 
Table l. (continued) 

Ceus Weoa Species Weu Species Weu 

Acute Value Acute Vol ue Ante-Ciaroa i c 

Roak 0 (eg/L) Species (eg/L)b Rotioc 

6 20,000 Widge, 20,000 

Paratanl!tarsus 

J 

parthenaqeneticus 

5 7,300 Hydra, .. 7,300 

Hydra sp. 

4 5,500 fathead minnow, 5,500 9.726 

Pimepholes promelas 

760 Amphipod, 760 

Hlfalella ~ 

2 597.2 Cladoceran, I ,450 2. 651 

\JI Daphnia magna 

" Cladoceran, 246 

Daphnia pulicaria · 

65.38 Amphipod, 65.38 

Gammarus (!Seudol imnaeus 
Table l. (continued) 

Genus Uean Species Uean Species Ueaa 

Acute Vain Acute Value Acute-CIIronic 

Rant 0 (ug/L) Species (ug/L)b Ratio c 

SALTWAT£R SP£CI£S 

Seleniu• (IV). 

15 17,350 fourspine stickleback, 11,350 

Apeltes quadracus 

14 14,650 Winter flounder, 14,650 

Pseudopleuronectes 

omericanus 

13 >I 0, 000 81 ue mussel, >I 0, 000 

Wytilus edu I is 

12 >10,000 Pacific oyster, >10,000 Vl 

()0 Crassostreo ~ 

II 9,725 Atlantic silverside, 9,725 

Wenidio menidia 

I 0 7,400 Sheepshead mj nnow. 7,400 10.96 

Cyprinodon varieqotus 

9 4,600 Blue crob, 4,600 

Co llj ~ect es sapid us 

8 4,400 Pinfish, 4,400 

Laqodon rhomboides 
Vl 

~ 

Table J. (co11tillued) 

Genus Mean Species Ueu Species Ueu 

Ac.te Value Acute Value Acute-CIIra• i c 

Rank a (f1q/L) Species C,q/Lib Ratio c 

7 3,497 Summer flounder, 3,497 

Porolichthvs dent at us 

6 I, 550 Striped bass, I, 550 

Worone soxot i I is 

5 I, 500 Wysid, I, 500 7.085 

Wysidopsis ~ 

4 I, 330 Copepod. 2,110 

A <: o rt i o i.l..!.!!.ll 

Copepod, 839 

Acort i a tonso 

3 I, 200 Brown shrimp, I, 200 

Penoeus oztecus 

2 I, 040 Dun9eness crab, I, 040 

Cancer magister 

599 Haddad, 599 

Welonoqrammus aeqlefinus 

a Ranked from most resistant to most sensitive based on Genus Wean Acute Value. 

Inclusion of "greater than" and "less than" values does not necessarily imply a true 

ranking, but does allow use of all genera for which dolo ore available so that the 

final Acute Value is not unnecessarily lowered. 

b from Table I. 

c rrom Table 2. 
en 

0 

Table l. (continued) 

Selenium( IV) 

rresh water 

rinal Acute Value= 371.8 ~giL 

Criterion Maximum Concentration= (371.8 ~giL) I 2 = 185.9 ~giL 

rinol Acute-Chronic Ratio= 8.314 (see text) 

rinal Chronic Value= (371 .8 pgll) I 8.314 = 44.72 ~giL 

rinol Chronic Value= 27.6 ~giL (lowered to protect rainbow trout; see text) 

Salt water 

rinal Acute Value= 587.7 ~giL 

Criterion Maximum Concentration = (587.7 ~giL) I 2 = 293.8 ~giL 

rinol Acute-Chronic Ratio = 8.314 (see text) 

rinol Chronic Value = (587.7 ~giL) I 8.314 = 70.69 ~giL 

Selenium(VI) 

rresh water 

rinol Acute Value= 25.65 ~giL 

Criterion Maximum Concentration = (25 65 ~giL) I 2 = 12.82 ~giL 

rinol Acute-Chronic Rotfo = 2.651 (see text) 

rinol Chronic Value= (25 65 ~g/l) I 2.651 = 9.676 rg/l 
Table 4. Toxicity or Seleniu• to Aquatic Plants 

Hardness 

(•g/l as Duration Concentration 

Species Che•icol ~lL (days) I!ill! (uq/L) 0 Reference 

rR£SHWAT£R SP£CJ£S 

Seleniu•(IV) .J 

Green olga, Sodium 90-120 Reduced 5,480 De Jong 1965 

Chiarello vulgaris seleni le growth 

Green olga, Sodium 14 Reduced 24,000 Woede et ol. 1980 

Scenedesmus dimorphus selenite growth 

Green olga, Sodium 8 Incipient 522 Bringmann and Kuhn 

Scenedesmus guodricoudo selenite inhibition 1977o;l978o,b;l979; 

1980b 

0\ Green olga, Sodium 8 Incipient 2,500 Bringmonn and Kuhn .... Scenedesmus guodricoudo selenite inhibition 1959o 

Blue-green olga, Sodium 8 Incipient 9,400 Bringmonn and Kuhn 

l,licrocystis aeruginiso selenite inhibition (9,300) 1976;1978o,b 

Blue-green olga, Sodium 14 Reduced 24,000 Woede et o I. 1980 

Anabaena cy I i ndr i ca selenite growth 

Blue-green alga, Sodium 6-18 LC50 15,000b Kumar and Prakash 

Anabaena voriobilis selenite 1971 

Blue-green olga, Sodium I 0-18 lC50 30,000b Kumar and Prakash 

Anacystis nidulons selenite 1971 

Green olga, Sodium 4 [C50 2,900 Richter 1982 

Selenastrum capricornutum selenite 
Tobie 4. (continued) 

Hardness 

(•g/L as Durot ioa Coaceatratioa 

Species Che•ical Coco3L (days) Hf ect (f,l~/q• Refereace 

Alga, 15 Reduced 5,g2o Borioud and llestre 

[ugleno groci I is growth 1984 

Duckweed, 4 £C50 2,400 Wong 1986 

lemno !!!l..!!.!u:. 

Seleniu•(VI) 

Blue-green olga, Sodium 14 Reduced 22,100 Woede et al. 1980 

Anoboeno cylindrico selenate growth 

Blue-green olga, Sodium 14 Reduced I 0,000 Vocke et ol. 1980 

Nicrocoleus vagi notus sel enote growth 0' 

N 

Green olga, Sodium 14 Did not re- I 0 Vocke et ol. 1980 

Ankistrodesmus selenate duce growth 

folcotus 

Green olga, Sodium 14 Reduced 22,100 Noede et ol. 1980 

Scenedesmus selenate growth 

dimorphus 

Green olga, Sodium 14 Reduced· I 00 Vocke et ol. 1980 

Scenedesmus sel enote growth 

obliquus 

Green alga, Sodium 14 Reduced lOO Vocke et a I . 1980 

Selenastrum sel enote growth 

capricornutum 
Table 4. (continued) 

Hard11ess 

(•g/l as Dllrat i a• Coace.trat i oa 

Species Chetaical .£!£2lL (days) ill!£! (ug/L)a Refereace 

Green alga, Sodium 4 £C50 199 Richter 1982 

Selenastrum selenate 

capricornutum 

Blue-green algo, Sodium 6-18 £C50 l9,000b Kumar and Prakash 

Anocystis nidulons selenate lg7J 

Blue-green olga, Sodium I 0-18 £C50 11. ooob Kumar and Prakash 

Anabaena viriobilis selenate 1971 

SALTWAT£R SP£CI£S 

Seleniii•(VI) 

0\ 

w 

Di ot.om, Selenious 4 £C50 (reduction 7,930 U.S. EPA 1978 

Skeletonemo costotum acidc in chlorophyll o) 

Dinoflagellate, Selenium 70-75 Woximum 0.01-0.05 lindstrom 1g55 

Peridinopsis borgei oxide growth 

° Concentration of selenium, not the chemical. 

b [stimoted from published groph. 

c Reported by Borrows et ol. (1980) in work performed under the some contract. 
Table 5. Biooccu•ulotion of Seleniu• by Aquatic Orgonis•s 

Hardness 

(•g/l OS Concentration Duration acr or 

Species Che•icol ~lL in Wafer (pg/Lt 0 ( doys l Tissue urb Reference 

rR£SHWAT£R SP£CI£S 

Seleniu•(IVl 

Rainbow trout, Sodium 325 48 Wuscle 2 Adams 1976 

ll.!..!!!2. gairdneri selenite 

Rainbow trout, Sodium 325 48 Whole body I Oc Adams 1976 

Salmo gairdneri selenite 

Rainbow trout (embryo), Sodium 135 308 Whole body 8 Hodson et a I . 

Salmo gairdneri selenite (past hatch) (estimate) 1980 

fathead minnow, Sodium 320-360 96 Muscle II. 6 Adams 1976 

0'\ Pimephales promelas selenite ~ 

fathead minnow, Sodium 320-360 96 Whale body 17.6 Adams 1976 

Pimephales promelos selenite 

81 ueg iII, Selenious 28 Whole body 20 Barrows et al. 

lepomis macrochirus acid 1980 

81 ueg iII, Sodium 25 10 120 Whole body 450 leml y 1982 

lepomis mocrochirus selenite 25 I 0 120 Whole body 470 

200 I 0 120 Whole body 430 

200 10 120 Whole body 460 

largemouth boss, Sodium 25 I 0 120 Whole body 310 leml y 1982 

l.ti cropterus solmoides selenite 25 I 0 120 Whole body 300 

200 I 0 120 Whole body 300 

200 I 0 120 Whole body 270 
Table 5. (continued) 

Hardness 

(•g/l OS Concentroti.on Duration acr or 

Species tll .. ical Caco3L in Water (uq/L) a (days) Tissue au• Reference 

Seleniu• VI 

Fathead minnow Sod i,um 107 56 Whole 52d Bertram and Brooks 

( 6-9 mo) , sel enote body 1986 

PimeJ!holes J!romelos 

Fathead minnow Sodium 21 '5 56 Whole 26d Bertram and Brooks 

( 6-9 mo) , selenate body 1986 

PimeJ!hales J!romelas 

Fathead minnow Sodium 43. 5 56 Whole 21d Bertram and Brooks 

( 6-9 mo) , set enote body 19B6 

PimeJ!hales J!romelos 

0\ 

VI 

SALTWATER SPECIES 

Seleniu•(IV) 

Euphausiid (adult), Sodium 28 Whole 200 fowler ond Benayoun 

Weganyct i phones norvegica selenite animal 1976c 

[uphaus i i d (adult), Sodium 28 Whale 8ooe fowler and Benayoun 

WegonyctiJ!hones norvegico selenite animal I 976c 

Shore crab (adult), Sodium 250 29 Ci II 14.40r Bjerregaard 1982 

Carcinus ~ selenite 

Shore crab (adult), Sodium 250 29 Hepato- 4.080f,g Bjerregaard I 982 

Carcinus ~ selenite pancreas 

Shore crab (adult), Sodium 250 29 Wuscle 2 88Uf ,g Bjerregoard 1982 

Carcinus ~ selenite 
"' 0\ 

Table 5. (continued) 

Salinity Concentration Duration Bcr or 

Species Ch-i cal (q/hl in Wafer (uq/lla (days) Tissue. BArb Refereace 

Seleniu• VI 

Striped boss Sodium 90 60 Whole No Increase Klouda 1985 

(juvenile, fed), selenate body 

~ 

J 

soxotilis 

Striped boss Sodium 90 60 Whole II. 78 Kl au do 1985 

(juvenile, starved), selenate body 

Worone soxotilis 

Striped boss Sodium I, 290 60 Whole 0.68 Kloudo 1985 

(juvenile, fed). selenate body 

~ soxotilis 

Striped boss Sodium I, 290 60 Whole 0.69 Koudo 1985 

(juvenile, starved), selenate body 

~ saxatilis 

a Measured concentration of selenium. 

b Bioconcentrotion factors (BCfs) and biooccumulotion factors (BAfs) ore based on measured concentrations of selenium in water 

and in tissue. 

c [stimated from graph. 

d Calculated by dividing the reported equilibrium concentration in. tissue (steady-state body burden) by the overage measured 

concentration in water. 

e Includes uptake from food. 

foetor was converted from dry weight to wet weight basis (see Guidelines). 

g Concentration of selenium was the some in exposed and control animals. 
lobi e 6. Other Data on [rfecfs or Seleniu• on Aquatic Organis•s 

Hardness 

(•g/L as Coace!lfrotion 

Species Che•icol ~.sL Dural ion [Heel (pg/L)a Reference 

rR£SHWAT£R SP£CI£S 

Seleniu•(IV) 

Green olga, Sodium 96 hr Inc-ipient i nhi- 2,500 Bringmonn and Kuhn 

Scenedesmus guodricoudo selenite bit ion {river 1959o,b 

water) 

Green olga, Sodium 72 hr Decreased dry 75 roe and Knight, 

Selenostrum coeri cor nut um selenite weight and Manuscript 

chlorophyll Q 

Green olga, Sodium 72 hr Bcr = 12-21b I 0-100 roe and Knight. 

Selenostrum coericornutum selenite Manuscript 

0\ 

...... Green olga, Sodium 72 hr Bcr = II ,164c ISO rae and Knight, 

Selenostrum capricornutum selenite llanuscript 

Alga, Selenious 30 days Increased 320 Wehr and Brown 1985 

ChrJ!SOchromulina acid growth 

breviturrita 

Algae {diatoms) , Sodium 18 days Inhibited II, 000 Patrick et a I . 1975 

IIi xed population selenite growth 

Bacterium, Sodium Incipient 90,000 Bringmonn and Kuhn 

[scherichio coli selenite inhibition 1959o 

Bacterium, Sodium 16 hr Incipient II, 400 Bringmann ond Kuhn 

Pseudomonus .I!..!!.!..Lll selenite inhibition (II • 200) 1976;1977o;l979;1980b 
Tobie 6. (continued) 

Hardness 

(•g/l as COic .. tratian 

Species Cll .. ical CaC03) . Duration !.!.!.!£!. (ug/L) 0 Reference 

Protozoon, Sodium 72 hr Incipient 1.8 Bringmann 1978; 

[ntosiphon sulcatum selenite inhibition (I . 9) Bringmann ond Kuhn 

1979;1980b;l981 

Protozoan, Sodium 28 hr Incipient 183,000 Bringmann and Kuhn 

Wicroregma heterostoma selenite inhibition 1959b 

Protozoan, Sodium 48 hr Incipient 62 Bringmann ond Kuhn 1981; 

Chilomonas paramecium selenite inhibition Bringmann et al. 1980 

Protozoan, Sodium 20 hr Incipient 118 Bringmann and Kuhn 

Uronema parduezi selenite inhibition 1980a;1981 

Sna i I, Sodium 7.5 days LT50 3,000 Van Puymbroeck et o I . 

0\ Lymnaea stagna I is selenite 1982 o:> 

Cladoceran, Sodium 48 hr ECSO (river 2,500 Bringmann and Kuhn 

Daphnia magna selenite wafer) 1959a,b 

Cladoceran, Sodium 214 24 hr LC50 16,000 Bringmann and Kuhn 

Daphnia magna selenite 1977a 

Cladoceran, Sodium 214 24 hr ECSO 9.9 Bringmann and Kuhn 

Daphnia magna selenite (swimming) 1977b 

'· 

Cladoceran, Sodium 329 48 hr EC50 710 Ha Iter et a I. 1980 

Daphnia magna selenite 96 hr (red) 430 

14 days 430 
Table 6. (continued) 

Hardness 

(•g/L as Conce.t rat i 011 

Species Che•icol ~1L Duratio• [ffect (fig/L) 0 Reference 

Clodoceron (<24 hr), Sodium 48 hr £C50 685 Ad oms ond Heidolph 

Dophnio mogno selenite 21 days (fed) 160 1985 

Clodoceron, Se1 en i ous 220d 48 hr LC50 I, 200 Kimball, Manuscript 

Daphnia mogno acid (fed) 

Ostracod, Sodium 100.8 48 hr LC50 130,000 Owsley 1984 

Cyclocypris sp. selenite 

Amphipod, Sodium 329 14 days LC50 70 Hoi ter et ol. 1980 

Hyalella ~ selenite (fed) 

Coho salmon (fry), Sodium 325 43 days LC50 160 Adams 1976 

Oncorhynchus kisutch selenite 

()\ 

\() Rainbow trout (fry), Sodium 334 21 days LC50 460 Adams 1976 

Solmo gairdneri selenite 

Rainbow trout (fry), Sodium 334 21 days Reduced 250 Ad oms 1976 

Solmo qairdneri selenite growth 

Rainbow trout, Sodium 330 5 days LC50 2,700 Adams 1976 

Salmo gairdneri selenite 2,750 

Rainbow trout, Sodium 325 48 days LC50 500 Adams 1976 

Salmo gairdneri selenite 

Rainbow trout, Sodium 325 96 days LC50 280 Adams 1976 

Solmo goirdneri selenite 
Table 6. (continued) 

Hardness 

(•g/l as Concentration 

Species Che•icol caco1L Durotio• [ffec:t t'ut/L) 0 Rererence 

Roi nbow trout, Sodium 135 9 days LCSO 7,020 Hodson et ol. 1980 

~ qoirdneri selenite 

Rainbow ' trout, Sodium 135 96 hr LCSO 7,200 Hodson et o I. 1980 

~ qoirdneri selenite 9 days (fed) 5,410 

Rainbow trout, Sodium 135 96 hr LCSO 8, 200 Hods on et ol. 1980 

Solmo qoirdneri selenite 9 days (fed) 6,920 

Rainbow trout, Sodium 135 41 days Reduced 47 Hodson et o I. 1980 

Solmo goirdneri selenite hatch of eyed 

embryos 

Rainbow trout. Sodium 135 SO wk Decreased iron 53 Hodson et ol. 1980 

Solmo goirdneri selenite in blood ...... 

0 

Rainbow trout (embryo) • Sodium 120 hr Did not reduce 10,000 Kloverkomp et ol. 

Solmo goirdneri selenite survival or 1983b 

time to hatch 

Rainbow trout, Sodium 272 90 days LCSO SS.2e Hunn et a I. 1987 

Solmo goirdneri selenite 

Northern pike, Sodium I 0. 2 76 hr LCSO II ,I 00 Kloverkamp et o I. 

[sox lucius selenite 1983a 

Goldfish, Selenium I 57 14 days LCSO 6,300 Cardwell et o I. 

Carassius ouratus dioxide 1976a,b 
Tobie 6. ( c:ont i nued) 

Hardness 

(•g/L as Conc:elfrat i oa 

Spec:ies Clae•i c:ol ...fill1L Duratioa !.!.ill! . Q lut/L) Refereace 

Goldfish, Sodium I 0 days Wort a I i ty 5,000 £IIi s 1937; £IIi s 

Carassius auratus selenite et a I . 1937 

Goldfish, Sodium 46 days. Gradual 2,000 £IIi s et al. 1937 

Carassius auratus selenite anorexia and 

mortality 

Goldfish, Selenium 7 days LCSO 12,000 Weir and Hine 1970 

Carassius auratus dioxide 

Goldfish, Selenium 48 hr Conditional 250 Weir and Hine 1970 

Carassius auratus dioxide avoidance 

Go I dfi sh, Sodium 24 hr acr = I. 42 0.45 Sharma and Davis 

Carassius auratus selenate acr = I. 15 0.9 1980 'I 

.- acr = I. 47 I. 35 

BCr = 0.88 2.25 

acr = I. 54 4.5 

rat head minnow, Sodium 338 48 days LCSO I ,I 00 Adams 1976 

Pimephales promelas selenate 

rathead minnow, Selenium 157 9 days LCSO 2,100 Cardwell et a I. 

Pimephales promelas dioxide 1976a,b 

rathead minnow, Sodium 329 96 hr LCSO I, 000 Halter et a I . 1980 

Pimephales promelas selenite (fed) 

ratheod minnow, Sodium 329 14 days LCSO 600 Halter et a I . 1980 

Pimephales promelas selenite (fed) 

rathead minnow, Selenious 220d 8 days LCSO 420 K i mba II, t.lanuscript 

Pimephales pramelas acid (fed) 
Table 6. (continued) 

Hardaess 

(ag/l as Co•co.trot i o• 

Species c .. alcal ~1L Duratio• ill.!ll (Hg/L) 0 Refere•c• 

Creek chub, Sol onium 48 hr llortality ll2, 000 Kim et al. 1977 

Semotilus otromoculotus dioxide 

.} 

Bl ueg iII, Sodium 318 48 days LCSO 400 Adams 1976 

lepomis macrochirus selenite 

Bl ueg iII, Selenium 157 14 days LCSO 12,500 Cardwell et al. 

lepomis macrochirus dioxide lg76a,b 

Yellow perch, Sodium I 0. 2 I 0 days LCSO 4,800 Klaverkomp et at. 

Perea flavescens selenite 1983 

African c I owed frog, Sodium 7 doys LCSO I, 520 Browne and Dumont 

Xenopus .!.illJ..! selenite 1979 

....... 

N African c I awed frog, Sodium 1-7 days Cellular domage 2,000 Browne and Dumont 

Xenopus laevis selenite 1980 

Seleniu•(VJ) 

Alga, 30 days Increased 50 Wehr and Brown 1985 

Chr~sochromulina growth 

breviturrita 

Sna i I , Sodium 6 days LTSO 15,000 Van Puymbroeck et a I. 

l~mnaea stagnalis selenate 1982 

Cladoceran, Sodium 129.5 7 days LCSO (fed} I, 870 Dunbor et a I . 1983 

Daphnia magna selenate 
Table 6. (continued) 

Hardaess 

(•g/l as Coaceetrotioe 

Species Cll-icol caco3L Durotioe Hfect fwi/Ll 0 Refereece 

Rainbow trout Sodium I 04 28 dors EC50 (death 5,000 Birge 1978; Birge and 

(embryo, larva), selenate (92-110) and deformity) (4,180) Bloc It 1977; Birge et al. 

Solmo goirdneri (5,170) 1980 

Goldfish Sodium 195 7 days EC50 (death 8,780 Birge 1978 

(embryo, I orva), selenate and deformity) 

Corossius ourotus 

Fathead minnow, Sodium 337.9 48 days LC50 2,000 Adams 1976 

Pimephales promelas selenate 

Fathead minnow, 51 .lO min No avoidance II ,200 Watenpaugh and 

Pimephales promelas Beitinger 1985o 

Fathead minnow, 24 hr LCSO 82,000 Wotenpaugh and ....... 

c.,.J Pimepholes promelas Beitinger 1985b 

Fathead minnow, 24 hr Reduced thermal 22,200 Watenpaugh and 

Pimephales promelas tolerance Beitinger 1986c 

Channel catfish Sodium 90 8.5-9 days Induced albinism Westerman and 

(embryo, fry), ~elenote Birge 1978 

lctalurus punctatus 

Narrow-mouthed toad Sodium 195 7 days £CSO (death and 90 Birge 1978; Birge and 

larva). 

'. deformity) (embryo, selenate Black 1977; Birge et at. 

Gostro(!hr~ne corolinensis 1979a 
Tobie 6. (continued) 

Salinity Concentration 

Species Che•ical (q/tq) Duration !.!.lli! ,,giL). Reference 

SALTWAT£R SP£CI£S 

Seleniu•(IV} 

J 

Anaerobic bacterium, Sodium 110 hr St imul oted 79.01 Jones and Stodtmon 

Wethonococcus vannielli selenite growth 1977 

Green olga, Sodium 32 14 days 5-12% increase 10-10,000 Wheeler et ol. 1982 

Chlorello sp. selenite in growth 

Green olga, Sodium 32 14 days 23% increase 100-10,000 Wheeler et ol. 1982 

Plotymonos subcordiformis selenite in growth 

Green alga, Sodium 32 20 days Increased 4,600 Gennity et at. 1985o,b 

Dunoliella l!rimolecto selenite growth; induced 

........ glutathione 

~ peroxidase 

Diatom, Selenium 29-30 72 hr No effect on 78.96 Thomas et ol. 1980o 

Thollossiosi ro oes t i vo I is oxide cell morphology 

Brown alga, Sodium !ill days 1355% increase 2.605 rr i es 1982 

~ Sl! i ro I is selenite in growth 

of tho IIi 

Red olga, Sodium 32 27 days Increase 4,600 Gennity et ol. 1985a,b 

Porl!hyridium cruentum selenite growth; induced 

glutathione 

peroxidase 
Table 6. (continued) 

Sol inity Concentration 

Species ClaHic:ol {o/kg) Duration illm {pg/L) 0 Refere11c:e 

Selelliu•(VI) 

Green olga, Sodium 32 14 days No effect on 10-1000 Wheeler et al. 1982 

Chiarello sp. seleno}e rate of cell 

Green olga, Sodium 32 4-5 days I 00% mortality 10,000 Wheeler et ol. 1982 

Chlorella sp. selenate 

Green olga, Sodium 32 14 days No effect on I 0-100 Wheeler et al. 1982 

Dunoliello erimolecto selenate rote of cell 

population growth 

Green olga, Sodium 32 14 days 71% reduction I, 000 Wheeler et a I. 1982 

Dunoliello erimolecta selenate in rate of cell 

population growth 

'-I 

VI Green olga, Sodium 32 4-5 days I 00% mo r to I i t y 10,000 Wheeler et ol. 1982 

Dunol iello erimolecta set enote 

Green olga, Sodium 32 14 days No effect 10 Wheeler et al. 1982 

Plat~monas subcordiformis selenate on rate of 

cell population 

growth 

Green alga, Sodium 32 14 doys · 16% decrease I 00 Wheeler et a I . 1982 

Plat~monas subcordiformis selenate i r rote of 

cell population 

growth 

Green alga, Sodium 32 14 days 50% decrease in I, 000 Wheeler et a I . 1982 

Plat~monas subcordiformis selenate rate or cell 

population 

growth 
Table 6. (continued) 

Saliaity Coaceatratioa 

Species o .. iul h/td hrotio• !.!ill! (ug_/L) 0 Refereace 

Green olga, Sodium 32 4-5 days 100% mortality 10,000 Wheeler et al. 1982 

Plotymonos subcordiformis selenate 

.I 

Brown olga, Sodium 60 days 160% increase 2.605 fries 1982 

~spiral is selenate in growth 

rote of thalli 

Red olga, Sodium 32 14 days 23-35% reduction 10-1000 Wheeler et ol. 1982 

Porphridium cruentum selenate in rote of cell 

population growth 

Red olga, Sodium 32 4-5 days I 00% mort o I i t y 10,000 Wheeler et ol. 1982 

Porphyridium cruentum sel enote 

........ [astern oyster (adult), Sodium 34 14 days No significant 400 fowler et ol. 1981 

"' Crossostreo virginico selenate effect on respirotion rote of g iII 

tissue 

Striped boss (embryo). Sodium 7.2-7.5 4 days 9.U successful 200,000 Kloudo 1985 

loforone soxotilis selenate hatch and 

survive 

Striped boss (larva), Sodium 4.0-5.0 4 days LC50 (control I 3, 020 Kloudo 1985 

Worone soxotilis selenate survivol=77%) 

Striped boss (juvenile), Sodium 3.5-5.5 9-65 days Significant 39-1.360 Klaudo 1985 

Worone soxotilis selenate incidence of 

development a nomalies of lower 

jaw 
Table 6. (confined) 

Species 

Striped bass (juvenile), 

~ saxatilis 

CliNical 

Sodium 

selenate 

J 

Sol hi tr 

(q/h) 

3.5-5.5 

a Concentration of selenium, not the chemical. 

Durotio• 

45 days 

b Converted from dry weight to wet weight basis (see Guidelines}. 

c Growth of algae was inhibited. 

d From Smith et al. (1976). 

Significant 

incidence of 

severe blood 

cytopathology 

Co•ce .. rot i a. 

(uq/L) 0 

I, 290 

e Calculated from the published data using probit analysis and allowing for 8.9% spontaneous mortality. 

Rerere•ce 

Klauda 1985 
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