# ~~EPA United Stat. Environmental Protection Agency Watar 

# Ambient OfficeofWater**EPA~/5-87-008** RegulationsandStandards September 1987 CriteriaendStandardlDivision washington.DC 20460 

# WaterQuality Criteria. for Selenium- 1987

### AMBIENTAQUATICLIFEWATERQUALITYCRITERIA FOR SELENIUM

U.S. ENVIRONMENTAL**PROTEC~ION**

### AGENCY

OFFICEOF RESEARCHAND DEVELOPMENT ENVIRONMENTALRESEARCHLABORATORIES 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 ProtectionAgency, 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 InformationService (NTIS), 5285 Port Royal Road, Springfield, VA 22161. Ordernumber: PB88-142 237

i iFOREWORD

Section 304(a)(l) of the CleanWater Act of 1977 (P.L. 95-217) requires the Administrator of the Environmental ProtectionAgency to publishwater 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 expectedfrom the presence of pollutants in any body of water. including ground water. This document is a revision of proposed criteria based upon considerationof 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, section304(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 inthis document are such scientific assessments. If water quality criteria associatedwith specific stream uses are adopted by a State as water 

### • quality standards under section303, 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 inother 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

LorenJ. Larson LarryT. Brooke (freshwater contributors) Universityof Wisconsin-Superior Superior, Wisconsin

Charles E. Stephan (document coordinator) Environmental ResearchLaboratory Duluth, Minnesota JeffreyL. Hyland JerryM. Neff (saltwatercontributors) Battelle Ocean Sciences Duxbury, Massachusetts

David J. Hansen (saltwatercoordinator) Environmental Research Laboratory Narragansett, Rhode Island

ivCONTENTS

Foreword...
. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . iii Acknowledgments.
. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . iv 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

Referenees.. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 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

viIntroduction Selenium is unique among pollutants because of its following attributes: 1. Selenium is located immediatelybelow 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, seleniumcan replace sulfur in some minerals and biologically important compounds (Ca11ahan et a1. 1979; Cooper et a1. 1974; Ewan 1979; Shamberger 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). Someof the proposed·modes of action of selenium involve reaction with or substitution for the sulfur in suchbiologically relevant natural compounds as sulfur-containing amino acids (Foe and Knight, Manuscript; Magos and Webb 1980). 2. Substantial quantities of seleniumenter 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. Seleniumalso occurs in sulfide deposits of copper, lead, mercury, silver, and zinc and canbe 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 seleniumthenenters 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)
canexist simultaneously in aerobic surface water at pH= 6.5 to 9.0. A fourth oxidation state (elemental =0) exists in sediment, but is insoluble inwater. Chemical conversion from one oxidation state to another oftenproceeds at sucha 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 (Burtonet 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 ina variety of ways, and Shrift (1964) postulated a seleniumcycle inwhich some species reduce the most oxidized form and others oxidize the reduced form(s). For example, organisms canoxidize elemental seleniumto 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 seleniumcanbe quite toxic, it has been shown to be an essential trace nutrient for many aquatic and terrestrial species and it

2ameliorates 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; Gatlinand Wilson 1984; Heisinger and Dawson 1983; Hilton et al. 1980; Hodson and Hilton 1983; Ostroumova 1986; Poston et al. 1976; Wilsonet al. 1984), an aquatic invertebrate (Cowgill et al. 1985,1986; Keating and Dagbusan 1984), and algae (Lindstrom 1984; Wehr and Brown 1985). In addition, seleniumprotects 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. Seleniumpretreatment 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). Seleniumaugmented accumulationof cadmium in some tissues of the shore crab, Carcinusmaenas (Bjerregaard 1982,1985). The available data do not show whether the various inorganic and organic compounds and oxidation states of seleniumare equallyeffective sources of seleniumas a trace nutrient or as protectionagainst pollutants. 6. Not onlyhas seleniumbeen demonstratedto be toxic to aquatic species when it is dissolved inwater, ithas also been demonstrated that uptake of seleniumfrom food canadversely affect aquatic species (e.g., Bennett et al. 1986; Goettl and Davies 1978; Hicks et al. 1984; Hiltonet al. 1980; Hodson and Hilton 1983) and mallardducks (Heinz et al. 1987; Hoffman and Heinz 1987). • 7. In some situations aquatic organisms accumulate more seleniumfrom 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 seleniumthat 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 thaneither selenium(IV) or selenium(VI). Fish accumulated selenomethioninemore efficientlythan selenium(IV) or selenium(VI) from boththe gastrointestinal tract (Kleinow 1984; Kleinow and Brooks 1986a) and from water (Sharma and Davis 1980). Sandholm et al. (1973) found that algae accumulated selenomethioninemuch 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, thanwere 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 breastmuscle when fed selenomethionine than when fed s e Ienium(IV)
. 9. The concentrationof 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.thanthe livers, whereas the converse was true at higher concentrations (Hilton et al. 1982; Hodson and Hilton 1983; Hodson et al. 1980). Similarly,
..he relative distributionof selenium in tissues of shrimp depended on whether the seleniumwas accumulated from water or from food (Fowler and Benayoun 1976b). Also, Heinz et al. (1987) found that when mallards were fed selenium(IV), more seleniumwas deposited in the egg yolk than in the egg white. When mallards were fed selenomethonine, however, more seleniumwas found in the white than in the yolk. In addition, the relative distributionbetween tissues might depend on the duration of the exposure and on whether the organisms are in the uptake or depuration phase {Kleinowand Brooks 1986a).

5

### 10. Seleniumoccurs ina varietyof forms inorganisms. Because of "alkali disease" and "blind staggers" among livestock, the characterizationof selenium interrestrial plants has receivedmuch attention. The water-soluble fraction from plants contained selenite, selenate, seleno-amino acids, and possiblyothercompounds. 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; Burtonet 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 seleniumand to decide how**~he** 

### data shouldbe interpreted and used to derive aquatic life water quality criteria for selenium. On the otherhand, comparisonof the form and locationof selenium in affected and unaffected organisms from laboratory and field exposures might be helpful indetermining the route by which aquatic organisms in field situations accumulate toxic amounts of selenium. Unless otherwise noted, all concentrations of selenium inwater reported herein from toxicity and bioconcentrationtests are expected to be essentially equivalent to acid-soluble seleniumconcentrations. All concentrations are

6expressed as selenium, not as the chemical tested. AlthoughVI 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, itwas assumed that when IV was introduced into stockor 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, itwould 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 Protectionof 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 inJuly, 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 durationof the test increased. For example, Halter et al. (1980) reported the LC50 for the amphipod, Hyalella azteca, to be 940 pg/L at 2days, 340 pg/Lat 4days, and 70 pg/Lat 14 days. (AlthoughHalter et al. (1980) did not specify the oxidation state used intheir studies, Adams and Johnson (1981) statedthat the tests were conductedon sodium selenite.) Similarly, Adams (1976) reported that the average LC50 for the rainbow trout, Salmo gairdneri, was 4,350 pg/Lat 4days, 500 pg/L at 48 days, and 280 pg/Lat 96 days, and for the fathead minnow, Pimephales promelas, the average LC50 was 10,900pg/Lat 4days and 1,100 at 48 days. Adams (1976) found that the acute toxicityof selenium(IV) to the fathead minnow was related to water tempe;ature with average 96-hrLC50s of 10,900pg/L at 13°C, 6,700pg/Lat 20°C, and 2,800pg/L at 25°C. Adaphnid, a midge, and the stripedbass, Morone saxatilis were more sensitive to selenium{IV) insoft than inhardwater (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 seleniumby 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 boththe most sensitive and most resistant freshwater species to selenium(IV) withacute values ranging from 210 pg/L for the crustacean, Daphnia magna (Adams andHeidolph 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 35,000pg/L for the common carp, Cyprinus carpio (Sato et al. 1980).

8Boyum (1984) reported a 48-hrLC50 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 inthe lowest concentrationtested was only47% inthe test that produced the LC50 of 6**~g/L.** Because of the highmortality 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 calculatedto be 371.8**~g/L** using the procedure described inthe Guidelines and the Genus Mean Acute Values inTable 3. The Final Acute Value is higher than the lowest Species Mean Acute Value.

9

### Acute toxicity data that canbe used to derive a saltwatercriterionfor selenium(IV) are available for eight**speci~s** 

### of invertebrates and eight species of fish that are resident inNorthAmerica (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 slightlywider 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 salinityon the toxicityof selenium(IV) to saltwater animals. Acute tests withthe copepod, Acartia tonsa, at·5 and 10°C gave similar results (Lussier 1986). Of the fifteen genera for which saltwatermean acute values are available (Table 3), the most sensitive genus, Melanogrammus, is nearly 29 times more sensitive thanthe most resistant, Apeltes. The sensitivities of the four most sensitive genera differby a factor of only 2.1. and these four include three invertebrates and one fish, which is the most sensitive of the four. The saltwaterFinal Acute Value for selenium(IV) is 587.7**~g/L,** 

### which is slightly lower thanthe lowest SpeciesMeanAcute 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

10amphipod, Hyalella azteca, withan 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 beenconducted on selenium(VI). Five 96-hr exposures resulted inLC50s ranging from 2,300 to 12,500**~g/L.** One test (Spehar 1986) was a flow-through test inwhich the concentrations were measured. The tests conducted withthe 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 withLC50s ranging from 20,000**~g/L** for a midge, Paratanytarsus parthenogeneticus, to442,000**~g/L** for a leech, Nephelopsis obscura.· 

### Of the elevengenera 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 substantiallybelow 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 andjuvenile stripedbass, respectively.

11

### Species Mean Acute Values have been determined for both selenium(IV) and selenium(VI) withtenfreshwater species (Table 3) and one saltwater species (Table 1). For tenof 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) withthis 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 thanthat 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 inTable 2. Chronic toxicitytests have beenconducted on selenium(IV) with five freshwater species, four of which are acutely sensitive species (Table 3). The rainbowtrout is boththe most acutely resistant of these five species, and the most chronically sensitive, and thus has amuch larger acute-chronic ' 

### ratio thanthe 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 similarto 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, eventhoughno control fish were deformed. Hodson et al. (1980) found that 47 to 53**~g/L** 

### caused a small

12reduction 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) indicatedthat the acute-chronic ratio was less than 187.2, and the data of Hodson et al. (1980) gave a ratio of 141.5. In90-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 concentrationof calcium inbone of rainbowtrout. However, the expected resultingdecrease in the toughness and/or strength of the bone did not occur. A90-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 divisionof an LC50 by 2to calculate a concentrationthat will not severely affect too many of the organisms. Divisionof 55.2**~g/L** by 2 results in27.6**~g/L.** The other four freshwater species withwhich chronic tests have been conducted on selenium(IV), including one fish species, are a'll acutely more sensitive, and chronicallymore resistant, than the rainbowtrout. Kimball (Manuscript) conducted an early life-stage test on selenium(IV) with fathead minnows. 

### Aselenium(IV) concentrationof 153**~g/L** reduced survival by 32% and reduced weight by 18.5%. At a concentrationof 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 reproductionof 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 testwithDaphnia 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 reportedby Adams and Heidolph (1985) was conducted ina 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 inthe test solutions were not adequatelymeasured. Aconcentrationof 200**~g/L** 

### severely affected all four generations, and the amount of effect increasedwitheach successive generation. Aconcentrationof 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 reprodictionof Daphnia pulex ina 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 greaterthan those of the control daphnids, even though some differences were observed for some broods during the test. Aconcentration of 800**~g/L** 

### causedabout a 40% reduction inthe mean total number of live young per adult. The resulting chronic value was 692.8**~g/L** 

### and the acute-chronic ratiowas 5.586. Data on the chronic toxicityof selenium(IV) are available for two saltwater species, the mysid, Mysidopsis bahia, and the sheepsheadminnow, Cyprinodon variegatus (Table 2). The life-cycle test withMysidopsis bahia

14was startedwith 48-hr post-releasejuveniles and lasted for 28 days (Ward et al. 1981). Exposure to concentrations of 320**~g/L** or greater significantly reduced survival of the first-generationmysids. 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 reproductionwere 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 afterhatch to measure survival and growth of juveniles. Percent hatch was reduced 0to 4% by concentrations of 970, 1,900, and 3,600**~g/L.** Survival ofjuveniles was reduced·4% by 470**~g/L,** 24% by 970**~g/L,** and more than 90% at higher concentrations. Growth was reduced 8% by seleniumconcentrations 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) withthree of the sevenmost 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 rainbowtrout was not used inthe calculationof the Final Acute-Chronic Ratio because this is an acutely resistant species. Divisionof the Final Acute Values by the Final

15

### Acute-Chronic Ratio results infreshwater and saltwaterFinal Chronic Values of 44.72 and 70.69**~g/L,** 

### respectively. Based on the data reported by Hunn et al. (1987) for rainbowtrout, 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 thanthe two saltwater chronic values, but neitherof the saltwater species withwhich chronic tests have been conducted is acutely sensitive to selenium(IV). Selenium(VI) Chronic tests have beenconducted on selenium(VI) with three freshwater species (Table 2). Some additional chronic tests have been conductedby 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 productionby 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 seleniumwere 0, 50, 100, 500, and 1,000**~g/L.** 

### Inone test withDaphnia magna and inone test with

### Q. pulicaria, the animals were fed algae that had grown for 48 hours in the same concentrationof selenium(VI) to which the daphnids themselves were exposed. Inthe third test, 

### Q. magna was fed algae that had been raised in control water. Inthis thirdtest, the intrinsic growth rate was reduced 527. at the concentration of 50**~g/L.** 

### Inthe tests inwhich the algae contained selenium, the intrinsic growth ratesof

### 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. pulicariawas affectedmore than

### Q. magna at each
16concentrationof selenium. Also at eachconcentrationof selenium, 

### Q. magna was affected less when it received selenium from both food and water thanwhen it received seleniumfrom onlywater. Separate tests showed that selenomethionine inwater 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 dilutionwater 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 rainbowtrout. No fish survived at 6,300**~g/L** or higher concentrations. A concentrationof 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 andBrooks 1986) to simulate a food chain inwater that contained the same concentrationof selenium(VI). Although a malfunction of the diluter causedthe concentrationof 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 inthat the more acutely sensitive species have a lower ratio (Table 3). Because it is meant to applyto sensitive species, the Final Acute-Chronic Ratio was set equal to 2.651, the ratio obtainedwiththe most acutely sensitive species with which achronic test has been conducted. Divisionof 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 substantiallybelowthe three available experimentally determined chronic values. No data are available concerning the chronic toxicity of selenium(VI) to saltwater animals. Chronic toxicity tests have beenconducted on both selenium(IV) and selenium(VI) with three species (Table 2). With all three species, selenium(IV) was 5to 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 othereight ratios are all between 2.6 and 17. Toxicityto Aquatic Plants Selenium(IV)**~** 

### Data are available on the toxicityof selenium(IV) to nine species of freshwater algae (Table 4). Results ranged from an LC50 of 30,000pg/L for the blue-greenalga, Anacystis nidulans (Kumar and Prakash 1971) to 522**~g/L** 

### for incipient inhibitionof the greenalga, Scenedesmus guadricauda (Bringmann and Kuhn 1977a,1978a,b,1979,1980b). Foe and Knight (Manuscript) found that 75 pg/L decreasedthe dryweight of Selenastrum

18capricornutum (Table 6). Wehr and Brown (1985) reported that·320**~g/L** increased the growthof 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-hrEC50 for the saltwater diatom, Skeletonema costatum, is 7,930**~g/L,** based on reduction inchlorophyll.!. (Table 4). Growth of Chlorella sp., Platymonas subcordiformis, and Fucus spiralis increased at selenium(IV) concentrations from 10 to 10,000**~g/L** (Table 6).· These data suggest that saltwaterplants will not be adversely affected by concentrations of selenium(IV) that do not affect saltwater animals. Selenium(Vt) Growth of several species of greenalgae were affectedby 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 inbodies of water susceptible to nuisance algal blooms. For example, Patricket 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-greenalgae. 

### ' 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 growthof Porphyridium cruentum (Wheeler et al. 1982). Although selenium(IV) appears to be more acutely and chronicallytoxic 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 stimulatedgrowthof Chrysochromulina breviturrita (Wehr and Brown 1985.) On the otherhand, selenium(VI) is more toxic than selenium (IV) to the freshwater Selenastrumcapricornutum (Richter 1982) and the saltwaterChorella sp. and Platymonas subcordiformis (Wheeler et al. 1982). In addition, Fries (1982) found that growth of thalli of the brown macroalga, Fucus spiralis, was stimulatedmore by exposure to selenium(IV) at 2.605**~g/L** 

### thanto the same concentrationof selenium(VI). AFinal Plant Value, as defined in the Guidelines, cannot be obtained because no test inwhich the concentrations of selenium(IV) or selenium(VI) were measured and the endpoint was biologically important has beenconducted with an important aquatic plant species.
Bioaccumulation Selenium(IV) Bioconcentration factors (BCFs) for selenium(IV) that have been obtained with freshwater species range from 2for the muscle of rainbow trout to 452 for the bluegill (Table 5). Adams (1976) studiedbothuptake and elimination of selenium-75 by fathead minnows at average concentrations of 12, 24, and 50**~g/L.** 

### He found that concentrations inwhole 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 concentrationswere found inviscera, possiblydue to uptake of seleniumadhering to food. Eliminationof seleniumwas curvilinear and became asymptotic with the time axis after 96 days. Eliminationwas most
20rapid from the viscera with a half-life of 5.1 days, but the half-life of selenium inother tissues was greater than50 days. Adams {1976) also conducteduptake 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 withthe fathead minnow, the viscera containedmore seleniumthangill ormuscle. Based on his tests with the two species, Adams (1976) concludedthat there was an inverse relationship between BCF and the concentrationof selenium(IV) in water. Hodson et al. (1980) exposed rainbowtrout 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 inproportionto selenium(lV) inwater. Barrows et al. (1980) exposed bluegills to selenious acid for 28 days. They reporteda maximum BCF inthe 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 enoughto 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. Forbluegills, the geometric mean whole-body BCF at 20° and 30°C was 452. For largemouthbass 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 incleanwater, selenium concentrations remained unchanged in spleen, liver, kidney, and white muscle, but the half-life for selenium ingills and erythrocytes was less than 15 days. 21

### Steady-state BCFs withtwo saltwater species ranged from 2.88 inchela muscle of adult shore crab, Carcinusmaenas (Bjerregaard 1982,1985) to 200 in whole adult euphausiids, Meganyctiphanes norvegica (Fowler and Benayoun 1976c). Seleniumwas accumulatedtoahigherconcentration in gill than in hepatopancreas ormuscle of the shore crab during exposure to 250**~g/L.** 

### The authors suggested thatmuch of the selenium associatedwiththe gill might be sorbedto the gill surface. Ingestionof food organisms that had been exposed to selenium(IV) canbe an important source of exposure of fish to selenium (Hodson and Hilton 1983; Sandholm et al. 1973; Turner and Swick 1983). Additionof selenium(IV) to food reduced survival of rainbow trout (Goettl and Davies 1978). Rudd and Turner(1983a,b) found that the bioaccumulationof seleniumby fish was reduced by sediment and by increasedprimaryproductivity. Fowler and Benayoun (1976) reportedthat the BAF for selenium(IV) from food plus water was four times higher for an euphausiid thanthe BCF (uptake from water alone). The blue mussel, Mytilus edulis, accumulated seleniumat a slow rate when exposed to selenium(IV), but didnot accumulate seleniumwhen exposed to bis(2-carboxybenzyl)selenium (Pelletier 1986a). Selenium{VI) Bertram and Brooks (1986) exposed adult fathead minnows to sodium selenate inwater, in food, and in food and water together. The food was specially**~** 

### preparedby raising algae in amedium 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-statewithin28 days. The whole-body BCFs ranged from 21 to 52 and decreased as the concentration inwater increased (Table 5). Uptake of selenium(VI) from food alone or from food and water together did not reach

22steady-state in eight and elevenweeks, respectively. Uptake from food and water were additive. Whenjuvenile striped basswere 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 bioconcentratedmore than selenium(VI) by saltwater phytoplanktoncommunities (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 othermaximum acceptable concentration in tissue, as defined inthe Guidelines, is available for selenium and, therefore, no Final Residue Value canbe calculated.
Other Data Selenium(IV) Additional data on the lethal and sublethal effects**~f** seleniumon aquatic species are presented inTable 6. Bringmann and Kuhn (1959a,b,1976, 1977a,1979,1980b,1981), Jakubczaket al. (1981), and Patricket 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 inhibitionmight be statistically significant, its ecological importance is unknown. Jones and Stadtman (1977) reported stimulationof growth of an anaerobic bacteriumexposed to49**~g/L.** Selenium(IV) at a concentrationof 100**~g/L** did not affect crustaceancommunities in enclosures in a lake contaminated by mercury (Saiki et al. 1985).

23Short and Wilber (1980) reportedthat the calciumbalance·inthe crayfish, Orconectes immunis, was altered by a 30-day exposure to a selenium concentrationof 10**~g/L.** Hodson et al. (1980) found delayed mortality during a 4-dayperiod following cessationof exposure to selenium(IV). Hilton et al. (1982) studied the uptake from food, distribution, and eliminationof selenium(IV) by rainbowtrout. Mancini (1983) calculated detoxification rates for selenium invarious 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 inTable 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). Fatheadminnow larvae that were fed the contaminated rotifers weighed less than larvae that were fed control rotifers. Westerman and Birge (1978) exposed channel catfishembryos and newly hatched fry for 8.5 to 9 days to an unspecified concentrationof selenium(VI). Albinismwas observed in 12.1 to 36.97.of the fry during the five years of such exposures. The respiratory rate of the easternoyster, Crassostrea virginica, was unaffectedby 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-oldjuveniles died after four days at 87,000**~g/L.** Exposure ofjuvenile fish for up to 65 days to

24concentrations of selenium(VI) between 39 and 1,360pg/L caused developmental anomalies and pathological lesions.

Field Studies Studies on Belews Lake inNorth Carolina (e.g., Cumbie as quoted in Hodson et al. 1984; Cumbie and Van Horn 1978; Finley 1985; Lemly 1985a,b; Sorensenet al. 1984) and Hyco and CatfishReservoirs inNorthCarolina (Baumann and Gillespie 1986; Gillespie and Baumann 1986; Sager and Cofield 1984) ·suggest that seleniummight be more toxic to certain species of freshwater fish thanhas been observed inchronic toxicity tests. Other bodies of water inwhich the effects of seleniumon aquatic organisms have been studied include a farm pond in New York (Furr et al. 1979; Gutenmann et al. 1976), various lakes and reservoirs inColorado and Wyoming (Birkner 1978; Kaiser et al. 1979), a drainage system inSouthCarolina (Cherry and Guthrie 1978; Cherryet al. 1976,1979a,b,1984; Guthrie and Cherry 1976,1979), Martin· CreekReservoir inTexas (Garrett and Inman 1984; Sorensen and Bauer 1984a,b; Sorenson et al. 1982), and Kesterson Reservoir in**Californi~** (Burtonet 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 inthe 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 otherhand, it is likely thatmost ambient waters contain substantial concentrations of two or more oxidation states of selenium (see item 3on page 2). 2. Unless the investigatorcontrolsthe additionof the test material, rarely can a field study conclusivelypinpoint the cause of any observed effects, because it is possible that the effects were causedby a combinationof agents orby 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 inwater 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 theircombinations in food and inwater 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 canbe answered with properly designed field and laboratory studies. The severe effects that were observed on the fish community inBelews Lake have been attributed, withdiffering degrees of certaintyby various authors, to the 10**~g** 

### selenium/L inthe lake. Although selenium is certainlya good candidate for the cause of the observed effects, studies on Belews Lake cannot establisha cause-effect relationship because avariety of

26other inorganic and organic materials undoubtedly entered the lake with the selenium. Studies on otherbodies of water that contain selenium at concentrations in the range of 1to 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 studieshave attempted to confirm that selenium affected the fish community inBelews Lake. For example, Lemly (1982) exposed bluegills and largemouthbass 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 4months when kept in cages and died almost immediately when released into the lake (Cumbie as quoted inHodson 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:·withbluegills from Roxboro City Lake, which contained very little selenium. The young survived when females from Roxboro City Lake were mated withmales from either source. When females from Hyco Reservoir were mated withmales from either source, the young hatched but died before attaining the swim-up stage. The young that died also contained highconcentrations of selenium, which theymust have received from their mothers. It is, of course, possible that the young also received one or more toxicants in addition to selenium from theirmothers 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 culturedmealworms to four other bluegills. The nymphs contained 13.6**~g** selenium/g (wet weight). The four fish fed mealworms

27

### appearedhealthy 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 additionto selenium, because the nymphs provided proportionatelymore selenium, orbecause the nymphs containedamore toxic form of selenium. Several feeding studies have shown that aquatic species can be adversely affectedby consuming food that contains 10 to 13**~g** 

### selenium/g. Thus these studies support the idea that.the effects observedby Finley (1985) were causedby selenium. In two 42-week feeding studies, mortality of rainbow trout increasedwhen their food contained selenium(IV) at a concentrationof 9**~g/g** 

### (Goettl and Davies 1978). Hiltonet al. (1980) reported that when rainbowtrout 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 similareffects when trout consumed food containing 11 to 12**~g/g** 

### for sitteenweeks. In·a fourth feeding studywith rainbow trout, selenium(IV) at 11.4**~g/g** 

### (ona freeze-dried basis) reduced**g~owth** 

### and increasedmortality ina sixteen-weektest (Hicks et al. 1984). Although their tests on early life stages and smoltificationof chinook salmon were possibly confounded by the presence of other pollutants, the results reported by Hamiltonet 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-dayold ducklings perhenwas 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

28ducklings perhen, respectively. Food containing 10**~g** selenium/gas selenomethionine resulted innearly ten times as much selenium in eggs as did food containinc 10**~g/g** as selenium(IV). Selenomethionine resulted inmore selenium in egg white thanyolk, but the opposite was true with selenium(IV). These data tndicate that rainbow trout, chinook salmon, and mallard ducks
were affectedwhen they consumed food that contained selenium in the range of 10 to 13**~g/g.** Most of these studies were conductedby 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 observedby Finley (1985) were indeed causedby selenium and that the 10**~g/L** in Belews Lake caused the effects observed there. The concentrationof selenium inan unaffected upper arm of Belews Lake was near or belowthe detection limit of 5**~g/L** (North Carolina Department of Natural Resources and Community Development 1986). The freshwater CriterionContinuousConcentration {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 inTable 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 CriterionMaximum Concentrationwould be 19.98**~g/L.**
Unused Data Some data on the effects of seleniumon 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 conductedwithbrine shrimp, Artemia sp., were not used because these species are from a unique saltwaterenvironment. 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 ResearchCounciJ (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 Hutchinsonand Stokes (1975) did not specify the oxidation state of the seleniumused intheir tests. Data were not used when seleniumwas a component of an effluent, fly ash, formulation, mixture, sediment, or sludge (e.g., Burtonet al. 1983; ·Fava et al. 1985; Hall et al. 1984; Hamilton et al. 1986; Hildebrandet al. 1976; Jay and Muncy 1979; MacFarlane et al. 1986; Phillips and Gregory 1980; Ryther

## eial. 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 seleniumalone. Braddon (1982), Christensenand 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-Nielsenand Gissel-Nielsen 1973,1978; Greenberg and Kopec 1986; Nassos et al. 1980). Kaiser (1980) calculatedthe 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 stressedby 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 seleniumby 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 solutionwas not adequatelymeasured or varied too much, (e.g., Nassos et al. 1980; Sharma and Davis 1980). Reports of the concentrations of selenium inwild 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; Penningtonet 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 andAndreasen 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 inwater was too small or the range of the measured concentrations was too large.

31Summary 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, boththe 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.** ·Ina separate test, a 90-dayLC50 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 2to 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. Fishand 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 sheepsheadminnow, 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 concentrationof 7,930**~g/L,** selenium(IV) caused a 50% reduction in chlorophyll a in a test with the saltwater diatom, Skeletonema costatum, but

32growth 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 inchelamuscle of adult shore crabs, Carcinus maenas, to 200 inwhole adult euphausiids, Meganyctiphanes norvegica. Selenium(Vl) The acute toxicityof 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 withDaphnia magna, the fathead minnow, and the rainbowtrout. 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 andjuveniles 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 increasedby 10**~g/L.** Steady-state bioconcentration factors of 1to 16 were obtained withjuvenile 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 1.6to 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 5to 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 obtainedwith an acutely resistant species. In contrast to the data obtainedwithaquatic animals, selenium(VI) is either as toxic as or more toxic than selenium(IV) to aquatic plants. Selenium(IV) seems to be bioconcentratedmore than selenium(VI) by aquatic plants and animals. Salmonids and mallard ducks were severelyaffected when they**con~umed** 

### food that contained selenium at concentrations of 10 to 13**~g/g.** 

### It is likelythat the populations of several species of warmwater fishes were destroyed by selenium at a concentrationof 10**~g/L** 

### inBelews Lake.
National Criteria The procedures described inthe "Guidelines for Deriving Numerical National**Wat~r** 

### Quality**Cri~eria·**

### for the Protectionof Aquatic Organisms and TheirUses" indicate that, except possiblywhere a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affectedunacceptably if the four-day average concentration of selenium does not exceed 5.0**~g/L**

### more thanonce every three years on the average and if the one-hour average concentrationdoes not exceed 20**~g/L** 

### more thanonce every threeyears on the average. The procedures described inthe ''Guidelines for Deriving Numerical National Water Quality Criteria for the Protectionof Aquatic Organisms and TheirUses" indicate that, except possiblywhere a locally important species is very sensitive, saltwateraquatic organisms and their uses shouldnot be affected unacceptably if the four-day average concentration of selenium does not exceed 71**~g/L** 

### more thanonce every three years on the average and if

34the one-hour average concentrationdoes not exceed 300**~g/L** more thanonce every three years on the average. If selenium is as toxic to saltwater fishes inthe field as it is to freshwater fishes inthe field, the status of the fish community shouldbe monitored whenever the concentrationof selenium exceeds 5.0**~g/L** in salt water. Implementation Because of the variety of forms of selenium inambient water and the lack


# . of de(initive informationabout 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 interms of the total recoverable measurement 

### (U.S. EPA 1983a), but newer criteria for metals and metalloids have beenexpressed in terms of the acid-soluble measurement (1985b). Acid-soluble selenium (operationallydefined 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 seleniumto, and bioaccumulationof seleniumby, aquatic organisms. It is expected that the results of tests used in the derivationof the criteria would not have changed substantially if they had been reported interms of acid-soluble selenium. 

### 2. On samples of ambient water, measurement of acid-soluble seleniumwill probably measure all forms of seleniumthat are toxic to aquatic life or canbe readily converted to toxic forms under natural conditions. In**additi~n.** this measurement probably will not measure several forms, such

35as seleniumthat is occluded inminerals, 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. Althoughwater quality criteriaapply to ambient water, the measurement used to express criteria is likelyto be used to measure selenium in aqueous effluents. Measurement of acid-soluble selenium is expected to be applicable to effluents. If desired, dilution of effluentwith receiving water before measurement of acid-soluble seleniummight be used to determine whether the receivingwater candecrease the concentration of acid-soluble seleniumbecause 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, similarto 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 probablywill not substantially affect the result of the measurement of total acid-soluble selenium. However, acidificationmight not prevent oxidationor 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 separationor measurement at the time of collectionof the sample or special preservation to prevent conversion of
one oxidation state of seleniumto the other. 368. Ambient waters have much higher buffer intensities at a pH between 1.5 and 2.0 thanthey do at a pH between4 and 9 (Stumm and Morgan 1981) 9. Differences inpH withinthe 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 acidificationand 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 separatelymeasure 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 digestionprocedure. First, certain species of some metals and metalloids cannot be measured because the total recoverable method cannot distinguishbetween individual oxidation states. Second, in some cases these criteriawould 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

### seleniumor for measuring selenium inambient water or aqueous effluents, measurement of bothacid-soluble seleniumand total recoverable selenium in ambient water or effluent orbothmight be useful. For example, there might be cause for concernwhen 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 specifiedfor measuring selenium in ambient surface water will probably also be used tomonitor effluents. If effluents are monitored by measuring only the dissolvedmetals and metalloids, the effluents might contain some seleniumthat would not be measured but might dissolve, due to dilutionor change inpH or both, when the effluent is mixed with receiving water. Second, measurement of dissolved seleniumrequires filtration of the sample at the time of collection. Third, the dissolved measurement is .especially inappropriate for use with suchmetals as aluminum that can exist
as hydroxide and carbonate precipitates intoxicity tests and in effluents. Use of different methods for different metals and metalloids wouldbe unnecessarily complicated. For these reasons, it is recommended that aquatic life criteria for seleniumnot be expressed as dissolved selenium. As discussed inthe Water QualityStandards Regulation (U.S. EPA 1983b) and the Foreword to this document, awaterquality criterion for aquatic life has regulatory impact only after it has been adopted in a State water quality standard. Such a standard specifies a criterionfor a pollutant that is consistent with a particulardesignateduse. With the concurrence of the U.S. EPA, States designate one ormore uses for eachbody of water or segment thereof and adopt criteria that are consistent with the use(s) (U.S.EPA

381983c,1987). In each standard a State may adopt the national**~riterion,** if one exists, or, if adequatelyjustified, a site-specific criterion. Site-specific criteriamay 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 selectedby 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 "threeyears" is the Agency's best scientificjudgment of the average amount of time aquatic ecosystems should be provided between excursions (Stephanet al. 1985; U.S. EPA 1985c). However, various species and ecosystems react and recover at greatly differing rates. Therefore, if adequatejustification 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 inState water quality standards, for developing water quality-based permit limits and for designing waste treatment facilities requires selectionof an appropriate wasteload allocationmodel. Althoughdynamic 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)
.

39Table I. AcuteToxicity or Seleniu•toAquaticAni•als Hard1ess LC50 SpeciesUeu (•g/L as ar £C50 Acute.Value Species Methoda Che•ical 

### .£!!!!JL (ug/L)b (ug/L) Rererence rR£SHWAT£R SP£CI£S Seleniu•(IV) Hydra (odult), 

### s.

# .. Sodium I,700 I,700 Brooke et al. 1985 Hydra sp. selenite Leech (odult). S,

# .. Sodium 49 8 203,000 203,000 Brooke et al. 1985 Nephelopsis obscuro selenite SnoiI (adult). 

### s.

# .. Sodium 50.6 53,000 Brooke et al. 1985**~**hypnorum selenite SnoiI {adult), 

### s... Sodium 49.8 23,000 34,910 Brooke et ol. 1985 Aplexa hypnorum selenite**~** 0 SnaiI, 

### s. u Sodium 45.7 24,100 24,100 Reading 1979 Physo sp. selenite Cladoceron (<24hr), 

### s. u Sodium I00.8. 600 Owsley 1984; OwsIey Ceriodophnio offinis selenite and NcCouley 1986 Clodoceron (36-60hr), 

### s. u Sodium I00.8 720 OwsIey 1984 Ceriodophnio offinis selenite '. Clodoceron (84-108 hr). 

### s. u Sodium I00.& 640 Owsley 1984 Ceriodophnio offinis selenite Clodoceron (72-120 hr), 

### s. u Sodium 100.8 '480 (603.6 OwsIey 1984 Ceriodo11hnio offinis seleniteTobie I. (conlinued) Horduss LCSO SpeciesUe11 (•g/los or £C50 AcuteValu 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 [IIersieck 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 SpeciesMe
.. (•g/L"as or£C50 AcuteVat
.. 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 pseudolimnoeus selenite Amphipod (odult), 

### s... Sodium 53.6 I,700 2,704 Brooke 1987 Gommorus pseudolimnoeus selenite

·Amphipod, 

### 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 Tonytarsus 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 I0,490 Hodson et aI. 1980 Solmo gairdneri seleniteTable I. (continued) Har-dness LC50 SpeciesWean 

### (•g/l as or- £C50 Acute-Value Species Wetboda Che11ical caco3

### L (ug/L)b (ug/L) Refer-ence Brook trout (odult), 

### r.

# .. Selenium 157 I0,200 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 Satoet ol. 1980 Cyprinus carpio fathead minnow, S, u Sodium 312 I0,500 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 aI
. 1985 Pimephales promelas seleniteTable I. (coniinued) Hardaess LCSO SpeciesYeaa (•g/Las or£CSO**Ant~**Value Species Yetllod0 Che•ical caco1

### L b (eg/L) (f!g/L) Refereace rothead minnow (juvenile), 

### s. u Sodium 40 7,760 Yoyer and [Jiersieclt Pimepholes promelos selenite 1986 ratheodminnow (fry), r. JM 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 rotheadminnow, r. M Selenious 220d 970 I,601 Kimball, Pimephales promelas acid Manuscript**~ ~**  White sucker, r. M Sodium I0.2 29,000 Kloverkomp et ol. Cotostomus commersoni selenite 1983o White sucIter, 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 aI
. 1985 Morone soxotilis selenite Channel catfish (juvenile),

### s.

# .. Sodium 49.8 16,000 Brooke et ol. 1985 lctalurus eunctatus seleniteTobie I. (contiaued) Hardaess LCSO SpeciesMeaa {•g/Les or£CSO AnteVehe Species Metllod0 Ch-ical**~lL** (f!g/L)b (f!gAI Reference Channel catfish (juveniIe),

### 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 aI. 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 IuegiII, 

### r.

# .. Selenium 157 28,500 28,500 Cardwell et al. lepomis mocrochirus dioxide 1976a,b Yellow perch, 

### r.

# .. Sodium I0.2 11.1ooe II,700 K Iaverkomp et ol. Perea flovescens selenite 1983o
Seleniu•(VI} Hydro (adult). s'

# .. Sodium 53.6 7,300 7,300 Brooke et aI
. 1985 Hydra sp. selenate '· leech (adult). S, w Sodium 49.3 442,000 442,000 Brooke et oI
. 1985 Nephelopsis obscuro selenateTable I. (continued) Hardness LCSO SpeciesUeoa 

### (•g/l OS or [CSO AcuteValue Species Uetllod0 Che•icol Coco3

## L b (,g/L) (f!g/L) Reference SnoiI, 

### 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 aI. 1985 Gammarus pseudoIimnaeus selenote Amphipod (adult), S,

# .. Sodium 51.0 57 65.38 Brooke 1987 Gommorus pseudoIimnaeus 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 aI
. 1985 Paratanytarsus selenate parthenogeneticus Rainbow trout (juvenile), 

### s.

# .. Sodium 51.0 24,000 Brooke et aI
. 1985 Salmo gairdneri selenate Rainbow trout, f.

# .. Sodium 45 47,000 47,000 Spehar 1986 Salmo gairdneri selenateTable I. (contined) Hardeess LC50 SpeciesUeu 

### (•g/l OS or£CSO AcuteVal11e Species Uetllod0 

### ...f.!f!!1L b leg/q Che•icol (pg/L} Aefereace rathead minnow, S,

### u Sodium 323 II,800 Adoms 1976 Pimephales promeles selenate ' ratheadminnow, S, 

### u Sodium 323 II,000 Adams 1976 Pimepholes promeles selenate ratheadminnow, 

### s. u Sodium 323 12,500 Adams 1976 Pimephales promeles selenate ratheod minnow {juvenile), 

### s.

# .. Sodium 47.9 2,300 Brooke et aI
. 1985 Pimephales promelas selenate ratheod minnow, r.

# .. Sodium 46 5,500 5,500 Spehar 1986 Pimephales promelas selenote**~**
...... Channel catfish S,

# .. Sodium 51.0 66,000 66,000 Brooke et al. 1985 (juvenile), selenote lctalurus punctotus B

IuegiII {juveniIe), 

### s.

# .. Sodium 50.4 63,000 63,000 Brooke et aI. 1985 Leeomis mocrochirus selenateTobie I. {continued) LCSO SpeciesMen Soli1ify orECSO AnteVohe Species Uetllod0 Che•icol (g/tg) b 

# ,,,fl) (,g/L) Refere1ce SALTWATER SPECIES Seleniu•(IV) Bluemussel (embryo). 

### s.

### u Selenium 33.79 >10,000 >10,000 Wortin 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 Sodiurn 33.79 >10,000 >10,000 Glickstein 1978 Crossostreo**~** selenite Copepod (adult), s, u Selenious 30 2.II0 2,II0 Lussier 1986 Acorti o clousi 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 Cancermagister oxideTobie I. (continued) LCSO SpeciesWean Salinity or £C50 AnteValue Species Uethda Che•icol (q/td b fug/L} l,gll) Rererence Blue crab (juvenile), 

### s. u Sodium 30 4,600 4,600 Word et al. I981 Collinectes sopidus selenite Haddock (larva), 

### s. u Selenious 30 599 599 Cordin 1986 Welanogrommus oeglefinus acid Sheepsheod minnow 

### s. u Seleniaus 6,700 Heitmuller et aI. (Juvenile), acid 1981 Cvrinodon variegotus Sheepsheod minnow 

### r. w Sodium 30 7,400 7,400 Word et aI. 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 aI.**~** 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 ParaIichthys dentatus acidTable I. (contiaued) LCSO SpeciesIleal Sali1ify or£C50 luteVal
.. Species llethd0 Che•ical (g/kg) (ug/L)b 

# ,,,jq ReFereace Winter flounder (larva), 

### s. u Seleniaus 30 14,240 Cardin 1986 Pseudopleuronectes acid americanus Winter fIounder (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. bConcentration of selenium, not the chemical.

c Reported by Borrows et al. (1980) in work performed in thesame laboratory under the same contract. drrom Smith et al. (1976).

e Calculated from regression equation. Not used in calculation of Species Wean Acute Value because data.are available for amore sensitive life stage.Table2. ChroaicToxicityor Seleniu•toAquaticAni•als Hardness Cllronic (•g/L as li•its CllronicValu Species Test0 Che•ical 

### .£!9!3L (ug/L)b (fAg/L) Reference fR£SHIAT£R SP£CI£S Seteniu•llV) Clodoceron, LC Sodium 240-310 II0-237 161.5 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 I977 Vl 

# - Rainbow trout, [LS Sodium 135 >47d >47 Hodson et at. 1980 Solmo goirdneri selenite fathead minnow, £LS Selenious 220c 83-153 II2.7 K imboII. Wonuscript Pimephales promelos ocid 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 Solhity liaits Cllroaic Valu Species Test• Cheaical {g/tg) 

# ,,,!L)b (flg/L) SALTWATERSP£Cl£S Seleni"ua{IV) -1 Wysid, LC Selenious 26 140-l2Q. 211.7 Wysidopsis!.!!.h.l.! acid Sheepsheodminnow, ElS Sodium 27 470-970 675.2 Cyprinodon voriegotus selenite

0 LC =life-cycleor partial life-cycle; [LS =early life-stage. bWeasured concentrations of selenium.
c rrom Smith et ol. (1976). dNone 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

Coto3

### L

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. 1981Table 2. (continued) Hardness 

### {•g/l OS AcuteValue ChroaicValue Species 

### ..!!!23L (ug/L} (ug/L} !ill.! Rainbow trout, 30 12,500 88.32 I41.5 ll.!.m.2,gairdneri Rainbow'trout, 135 8,800 )47 <187.2 Salmo gairdneri ratheadminnow, 220 775.5a 112.7 6.881 Pimephales promelas Wysid, 26b I,500 211. 7 7.085 Wvsidopsis**~** Sheepsheodminnow, 27b 7,400 675.2 I0.96 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 ratheadminnow, 45-47 5,500 565.5 9.726 Pimephales promelas

aGeometric mean of two values in Table I. bSalinity (g/kg), not hardness.Table3. Raakecl Ge•us Yea• AcuteValues'witil Species Wean Acute-CIIra•ic Ratios Ge•us Yea• SpeciesWean SpeciesWeu AnteValue AnteValue Ante-CIIro•ic Rad0 (ug/L) Species (ug/L)b Ratioc rRESHWATER SPECIES Sele•i••(IV) 22 203,000 leech, 203,000 Nephelopsis obs·curo 21 42,500 Widge, 42,500 Tonytarsus dissimilis 20 35,000 Common corp, 35,000 Cyprinus carpio. 19 34,910 SnoiI, 34,910 \J1 Aplexo hypnorum J:- 18 30,180 White sucker, 30,180 Cotostomus commersoni 17 28,500 81uegiII, 28,500 lepomis macrochirus 16 26,100 Goldrish, 26 100 Carossius ourotus IS 25,930 Widge, 25,930 Chironomus plumosus 14 24,I00 SnoiI, 24,100 Physo sp.Table l. {continued) Ceaus Yean SpeciesYen SpeciesMeu AcuteValue AcuteValue Acute-Cbo•ic Ranta (f1g/L) Species (f1g/Llb . 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 I0 I0,490 Roinbow trout, I0,490 141.5 Solmo goirdneri 9 I0,200 Brook trout, I0,200 Solvelinus fontinolis \J1 \J1 8 6,500 Flogfish, 6,500 Jordonellofloridoe 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 soxotilisTable 3. (continued) Genus Yean SpeciesYean SpeciesYen AcuteValue AcuteValue Acute-CIIruic Rank0 (uq/L) Species (uq/L)b Ratioc 4 I,700 Hydra, I,700 Hydra sp. 3 I,601 Fatheadminnow_. 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 I0 193,000 SnaiI, 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 I6.26 Salmo gairdneriTablel. (continued) CeusWeoa SpeciesWeu SpeciesWeu AcuteValue AcuteVolue Ante-Ciaroaic Roak0 (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 (!SeudolimnaeusTable l. (continued) Genus Uean Species Uean SpeciesUeaa AcuteVain AcuteValue Acute-CIIronic Rant0 (ug/L) Species (ug/L)b Ratioc 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 >I0,000 81ue mussel, >I0,000 Wytilus eduIis 12 >10,000 Pacific oyster, >10,000 Vl ()0 Crassostreo**~** II 9,725 Atlantic silverside, 9,725 Wenidio menidia I0 7,400 Sheepshead mjnnow. 7,400 10.96 Cyprinodon varieqotus 9 4,600 Blue crob, 4,600 Collj**~ect**es sapidus 8 4,400 Pinfish, 4,400 Laqodon rhomboidesVl**~** TableJ. (co11tillued) Genus Mean SpeciesUeu SpeciesUeu Ac.teValue AcuteValue Acute-CIIra•i c Ranka (f1q/L) Species C,q/Lib Ratioc 7 3,497 Summer flounder, 3,497 Porolichthvs dentatus 6 I,550 Striped bass, I,550 Worone soxotiIis 5 I,500 Wysid, I,500 7.085 Wysidopsis**~** 4 I,330 Copepod. 2,110 A<:ortioi.l..!.!!.ll Copepod, 839 Acorti 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 tomost 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. bfrom Table I.
c rrom Table 2.en 0 Table l. (continued) Selenium(IV) rresh water rinal Acute Value= 371.8**~giL** CriterionMaximumConcentration= (371.8**~giL)** 

### I 2 = 185.9**~giL** rinol Acute-Chronic Ratio= 8.314 (see text) rinal Chronic Value= (371.8pgll) 

### I 8.314 =44.72**~giL** rinol Chronic Value= 27.6**~giL** (lowered toprotect rainbow trout; see text) Salt water rinal Acute Value= 587.7**~giL** CriterionMaximum 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** CriterionMaximumConcentration =(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 =9.676rg/lTable4. Toxicity or Seleniu•toAquatic 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 selenile 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 oI. 1980 Anabaena cyI indrica selenite growth Blue-green alga, Sodium 6-18 LC50 15,000b Kumar and Prakash Anabaena voriobilis selenite 1971 Blue-green olga, Sodium I0-18 lC50 30,000b Kumar and Prakash Anacystis nidulons selenite 1971 Green olga, Sodium 4 [C50 2,900 Richter 1982 Selenastrumcapricornutum seleniteTobie4. (continued) Hardness (•g/L as Durotioa Coaceatratioa Species Che•ical Coco3

## L (days) Hfect**(f,l~/q•** Refereace Alga, 15 Reduced 5,g2o Borioud and llestre [ugleno grociIis 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 I0,000 Vocke et ol. 1980 Nicrocoleus vaginotus selenote growth 0' N Green olga, Sodium 14 Did not re- I0 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· I00 Vocke et ol. 1980 Scenedesmus selenote growth obliquus Green alga, Sodium 14 Reduced lOO Vocke et aI
. 1980 Selenastrum selenote growth capricornutumTable4. (continued) Hard11ess (•g/las Dllratia• Coace.tratioa 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 I0-18 £C50 11.ooob Kumar and Prakash Anabaena viriobilis selenate 1971
SALTWAT£R SP£CI£S Seleniii•(VI) 0\ w Diot.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 thesome contract.Table5. Biooccu•ulotionof Seleniu•by AquaticOrgonis•s Hardness (•g/l OS Concentration Duration acr or Species Che•icol**~lL** inWafer (pg/Lt0 (doysl 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 IOc Adams 1976 Salmo gairdneri selenite Rainbow trout (embryo), Sodium 135 308 Whole body 8 Hodson et aI
. 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 81uegiII, Selenious 28 Whole body 20 Barrows et al. lepomis macrochirus acid 1980 81uegiII, Sodium 25 10 120 Whole body 450 lemly 1982 lepomis mocrochirus selenite 25 I0 120 Whole body 470 200 I0 120 Whole body 430 200 10 120 Whole body 460 largemouth boss, Sodium 25 I0 120 Whole body 310 lemly 1982 l.ticropterus solmoides selenite 25 I0 120 Whole body 300 200 I0 120 Whole body 300 200 I0 120 Whole body 270Table 5. (continued) Hardness 

### (•g/l OS Concentroti.on Duration acr or Species tll
.. ical Caco3

### L inWater (uq/L)a (days) Tissue au• Reference Seleniu•VI Fatheadminnow Sodi,um 107 56 Whole 52d Bertramand Brooks (6-9mo), selenote body 1986 PimeJ!holes J!romelos Fatheadminnow Sodium 21'5 56 Whole 26d Bertramand Brooks (6-9mo), selenate body 1986 PimeJ!hales J!romelas Fatheadminnow Sodium 43.5 56 Whole 21d Bertramand Brooks (6-9mo), setenote body 19B6 PimeJ!hales J!romelos 0\ VI SALTWATER SPECIES Seleniu•(IV) Euphausiid (adult), Sodium 28 Whole 200 fowler ond Benayoun Weganyctiphones norvegica selenite animal 1976c [uphausi id (adult), Sodium 28 Whale 8ooe fowler and Benayoun WegonyctiJ!hones norvegico selenite animal I976c Shore crab (adult), Sodium 250 29 CiII 14.40r Bjerregaard 1982 Carcinus**~** selenite Shore crab (adult), Sodium 250 29 Hepato- 4.080f,g Bjerregaard I982 Carcinus**~** selenite pancreas Shore crab (adult), Sodium 250 29 Wuscle 288Uf,g Bjerregoard 1982 Carcinus**~** selenite

## "' 0\ Table 5. (continued) Salinity Concentration Duration Bcr or Species Ch-ical (q/hl inWafer (uq/lla (days) Tissue. BArb Refereace Seleniu•VI Striped boss Sodium 90 60 Whole No Increase Klouda 1985 (juvenile, fed), selenate body J**~** soxotilis Stripedboss Sodium 90 60 Whole II.78 Klaudo 1985 (juvenile, starved), selenate body Worone soxotilis Stripedboss 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. bBioconcentrotion factors (BCfs) and biooccumulotion factors (BAfs) ore based on measured concentrations of selenium in water

and in tissue.

c [stimated from graph. dCalculated by dividing the reported equilibriumconcentration in.tissue (steady-state body burden) by the overagemeasured concentration in water.
e Includes uptake from food. foetor was converted from dry weight to wet weight basis (see Guidelines). g Concentration of seleniumwas the some in exposed and control animals.lobie 6. OtherData on [rfecfsor Seleniu•on Aquatic Organis•s Hardness (•g/L as Coace!lfrotion Species Che•icol**~.sL** Duralion [Heel (pg/L)a Reference rR£SHWAT£R SP£CI£S Seleniu•(IV) Green olga, Sodium 96 hr Inc-ipient inhi- 2,500 Bringmonn and Kuhn Scenedesmus guodricoudo selenite bition {river 1959o,b water) Green olga, Sodium 72 hr Decreased dry 75 roe and Knight, Selenostrumcoericornutum selenite weight and Manuscript chlorophyll Q Green olga, Sodium 72 hr Bcr

### =12-21b I0-100 roe and Knight. Selenostrumcoericornutum selenite Manuscript 0\

...... Green olga, Sodium 72 hr Bcr

### =II,164c ISO rae and Knight, Selenostrumcapricornutum 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 aI
. 1975 IIixed 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;1980bTobie6. (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 SnaiI, Sodium 7.5days LT50 3,000 Van Puymbroeck et oI
. 0\ Lymnaea stagnaIis 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 HaIter et aI. 1980 Daphnia magna selenite 96 hr (red) 430 14 days 430Table 6. (continued) Hardness (•g/L as Conce.trati011 Species Che•icol**~1L** Duratio• [ffect (fig/L)0 Reference Clodoceron (<24 hr), Sodium 48 hr £C50 685 Adoms ond Heidolph Dophnio mogno selenite 21 days (fed) 160 1985 Clodoceron, Se1enious 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 Hoiter 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 Adoms 1976 Solmo qairdneri selenite growth Rainbow trout, Sodium 330 5days 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 seleniteTable6. (continued) Hardness 

### (•g/las Concentration Species Che•icol caco1

### L Durotio• [ffec:t t'ut/L)0 Rererence Roinbow trout, Sodium 135 9days LCSO 7,020 Hodson et ol. 1980**~** qoirdneri selenite ' Rainbow trout, Sodium 135 96 hr LCSO 7,200 Hodson et oI. 1980**~** qoirdneri selenite 9days (fed) 5,410 Rainbow trout, Sodium 135 96 hr LCSO 8,200 Hodson et ol. 1980 Solmo qoirdneri selenite 9days (fed) 6,920 Rainbow trout, Sodium 135 41 days Reduced 47 Hodson et oI. 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 aI. 1987 Solmo goirdneri selenite Northern pike, Sodium I0.2 76 hr LCSO II,I00 Kloverkamp et oI. [sox lucius selenite 1983a Goldfish, Selenium I57 14 days LCSO 6,300 Cardwell et oI. Carassius ouratus dioxide 1976a,bTobie 6. (c:ontinued) Hardness (•g/L as Conc:elfratioa Spec:ies Clae•ic:ol 

### ...fill1L Duratioa 

### !.!.ill! . Q lut/L) Refereace Goldfish, Sodium I0days WortaIity 5,000 £IIis 1937; £IIis Carassius auratus selenite et aI
. 1937 Goldfish, Sodium 46 days. Gradual 2,000 £IIis et al. 1937 Carassius auratus selenite anorexia and mortality Goldfish, Selenium 7days LCSO 12,000 Weir and Hine 1970 Carassius auratus dioxide Goldfish, Selenium 48 hr Conditional 250 Weir and Hine 1970 Carassius auratus dioxide avoidance GoIdfish, 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 rathead minnow, Sodium 338 48 days LCSO I,I00 Adams 1976 Pimephales promelas selenate rathead minnow, Selenium 157 9days LCSO 2,100 Cardwell et aI. Pimephales promelas dioxide 1976a,b rathead minnow, Sodium 329 96 hr LCSO I,000 Halter et aI
. 1980 Pimephales promelas selenite (fed) ratheodminnow, Sodium 329 14 days LCSO 600 Halter et aI
. 1980 Pimephales promelas selenite (fed) rathead minnow, Selenious 220d 8days LCSO 420 K imbaII, t.lanuscript Pimephales pramelas acid (fed)Table 6. (continued) Hardaess (ag/las Co•co.trotio• Species 

### c.. alcal**~1L** Duratio• 

### ill.!ll (Hg/L)0 Refere•c• Creek chub, Solonium 48 hr llortality ll2,000 Kim et al. 1977 Semotilus otromoculotus dioxide

.} BluegiII, Sodium 318 48 days LCSO 400 Adams 1976 lepomis macrochirus selenite BluegiII, Selenium 157 14 days LCSO 12,500 Cardwell et al. lepomis macrochirus dioxide lg76a,b Yellow perch, Sodium I0.2 I0days LCSO 4,800 Klaverkomp et at. Perea flavescens selenite 1983 African cIowed frog, Sodium 7doys LCSO I,520 Browne and Dumont Xenopus .!.illJ..! selenite 1979

....... N African cIawed frog, Sodium 1-7days 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 SnaiI, Sodium 6days LTSO 15,000 Van Puymbroeck et aI.**l~mnaea** stagnalis selenate 1982 Cladoceran, Sodium 129.5 7days LCSO (fed} I,870 Dunbor et aI
. 1983 Daphnia magna selenateTable 6. (continued) Hardaess (•g/las Coaceetrotioe Species Cll-icol 

### caco3

# L Durotioe Hfect fwi/Ll0 Refereece Rainbow trout Sodium I04 28 dors EC50 (death 5,000 Birge 1978; Birgeand (embryo, larva), selenate (92-110) and deformity) (4,180) BlocIt 1977; Birgeet al. Solmo goirdneri (5,170) 1980 Goldfish Sodium 195 7days EC50 (death 8,780 Birge 1978 (embryo, Iorva), selenate and deformity) Corossius ourotus Fathead minnow, Sodium 337.9 48 days LC50 2,000 Adams 1976 Pimephales promelas selenate Fathead minnow, 51 .lOmin No avoidance II,200 Watenpaugh and Pimephales promelas Beitinger 1985o Fatheadminnow, 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 8.5-9days Induced albinism Westerman and (embryo, fry),**~elenote** Birge 1978 lctalurus punctatus Narrow-mouthed toad Sodium 195 7days £CSO (death and 90 Birge 1978; Birge and larva). '. deformity) (embryo, selenate Black 1977; Birge et at.**Gostro(!hr~ne** corolinensis 1979aTobie 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 Stimuloted 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 Thollossiosiro oest ivoIis oxide cell morphology Brown alga, Sodium !ill days 1355% increase 2.605 rries 1982**~** Sl!iroIis selenite in growth of thoIIi Red olga, Sodium 32 27 days Increase 4,600 Gennity et ol. 1985a,b Porl!hyridiumcruentum selenite growth; induced glutathione peroxidaseTable 6. (continued) Solinity 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 4-5days I00% mortality 10,000 Wheeler et ol. 1982 Chlorella sp. selenate Green olga, Sodium 32 14 days No effect on I0-100 Wheeler et al. 1982 Dunoliello erimolecto selenate rote of cell population growth Green olga, Sodium 32 14 days 71% reduction I,000 Wheeler et aI. 1982 Dunoliello erimolecta selenate in rate of cell population growth '-I VI Green olga, Sodium 32 4-5 days I00% mortoIi ty 10,000 Wheeler et ol. 1982 Dunoliello erimolecta setenote 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 I00 Wheeler et aI
. 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 aI
. 1982**Plat~monas** subcordiformis selenate rate or cell population growthTable 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 60days 160% increase 2.605 fries 1982**~spiral**is selenate in growth roteof thalli Red olga, Sodium 32 14 days 23-35% reduction 10-1000 Wheeler et ol. 1982 Porphridiumcruentum selenate in rote of cell population growth Red olga, Sodium 32 4-5days I00% mortoIity 10,000 Wheeler et ol. 1982 Porphyridiumcruentum selenote

........ [astern oyster (adult), Sodium 34 14 days No significant 400 fowler et ol. 1981 

# "' Crossostreo virginico selenate effect on respirotion rote of giII tissue Striped boss (embryo). Sodium 7.2-7.5 4days 9.U successful 200,000 Kloudo 1985 loforone soxotilis selenate hatch and survive Striped boss (larva), Sodium 4.0-5.0 4days LC50 (control I3,020 Kloudo 1985 Worone soxotilis selenate survivol=77%) Striped boss (juvenile), Sodium 3.5-5.5 9-65days Significant 39-1.360 Klaudo 1985 Worone soxotilis selenate incidenceof development anomalies of lower jawTable 6. (confined) Species Striped bass (juvenile),**~** saxatilis CliNical Sodium selenate

J Solhitr (q/h) 3.5-5.5

a Concentration of selenium, not thechemical. Durotio• 45 days

b Converted from dry weight to wet weight basis (seeGuidelines}.

c Growth of algaewas inhibited. d From Smith et al. (1976). Significant incidenceof severeblood cytopathology Co•ce
..rotia. (uq/L)0

I,290

e Calculated from the published data using probit analysis and allowing for 8.9% spontaneousmortality. Rerere•ce Klauda 1985

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