United States Office of Water EPA-822-D-04-001
Environmental Protection 4304 November 2004
Agency
&EPA Draft
Aquatic Life
Water Quality Criteria
for Selenium
-2004
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Draft
Aquatic Life Water Quality Criteria for
Selenium
2004
November 2004
U.S. Environmental Protection Agency
Office of Water
Office of Science And Technology
Washington, D.C.
Draft November 12, 2004
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NOTICES
This document has been reviewed by the Health and Ecological Effects Criteria Division, Office
of Science and Technology, U.S. Environmental Protection Agency, and approved for
publication.
Mention of trade names or commercial products does not constitute endorsement or
recommendation for use.
This document can be downloaded from:
http://www.epa.gov/waterscience/criteria/aqlife.html
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ACKNOWLEDGMENTS
Dennis O. Mclntyre Larry T. Brooke
Tyler K. Linton University of Wisconsin-Superior
William H. Clement Superior, Wisconsin
Gregory!. Smith
Manoel Pacheco
Great Lakes Environmental Center
Columbus, Ohio
Charles Delos
(document coordinator)
USEPA
Health and Ecological Effects Criteria Division
Washington, D.C.
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Table of Contents
Introduction 1
Selenium Chemistry 1
Inorganic Selenium 2
Organoselenium 4
Departure from Thermodynamic Equilibrium 5
Physical Distribution of Species in Surface Water 5
Sources of Selenium to Aquatic Systems 6
Selenium Biogeochemistry 7
Narrow Margin Between Sufficiency and Toxicity 8
Selenium Document Information 10
Acute Toxicity of Selenite 12
Acute Toxicity of Se(IV) to Freshwater Animals 12
Hyalella (amphipod) 12
Ceriodaphnia (cladoceran) 12
Daphnia (cladoceran) 13
Hydra 13
Morone (striped bass) 13
Pimephales (fathead minnow) 13
Gammarus (amphipod) 13
Jordanella (flagfish) 13
Oncorhynchus (salmonid) 14
Lepomis (bluegill) 14
Se(IV) Freshwater Final Acute Value Determination 14
Acute Toxicity of Se(IV) to Saltwater Animals 15
Argopecten (bay scallop) 15
Melanogrammus (haddock) 16
Cancer (dungeness crab) 16
Penaeus (brown shrimp) 16
Acartia (copepod) 16
Americamysis (Mysidopsis) (mysid) 16
Spisula (surf clam) 16
Morone (striped bass) 17
Paralichthys (summer flounder) 17
Callinectes (blue crab) 17
Crassostrea (Pacific oyster) 17
Mytilus (blue mussel) 17
Pseudopleuronectes (winter flounder) 17
Se(IV) Saltwater Final Acute Value Determination 18
Acute Toxicity of Selenate 19
Sulfate-dependent Toxicity of Selenate 19
Sulfate Correction 19
Acute Toxicity of Se(VI) to Freshwater Animals (Sulfate Adjusted Values) 21
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Ceriodaphnia (cladoceran) 21
Hyalella (amphipod) 21
Daphnia (cladoceran) 21
Gammarus (amphipod) 22
Xyrauchen (razorback sucker) 22
Gila (bonytail) 22
Pimephales (fathead minnow) 23
Ptychocheilus (Colorado squawfish) 23
Oncorhynchus (salmonid) 23
Lepomis (bluegill) 24
Ictalurus (channel catfish) 24
Se(VI) Freshwater Final Acute Value Determination 24
Acute Toxicity of Se(VI) to Saltwater Animals 24
Se(VI) Saltwater Final Acute Value Determination 24
Comparison of Selenite and Selenate Acute Toxicity 25
Review and Analysis of Chronic Data 55
Selection of Medium for Expressing Chronic Criterion 55
Calculation of Chronic Values 58
Evaluation of Freshwater Chronic Data for Each Species 60
Brachionus calyciflorus (freshwater rotifer) 61
Oncorhynchus tshawytscha (chinook salmon) 61
Oncorhynchus mykiss (rainbow trout) 62
Oncorhynchus clarki (cutthroat trout) 64
Salvelinusfontinalis (brook trout) 64
Pimephales promelas (fathead minnows) 65
Catostomus latipinnis (flannelmouth sucker) 68
Xyrauchen texanus (razorback sucker) 68
Lepomis macrochirus (bluegill sunfish) 69
Morone saxitilis (Striped bass) 73
Formulation of the Final Chronic Value (FCV) for Selenium 74
National Criteria 82
Implementation 82
Appendices
A. Information Used in the Sulfate Correction of Selenate Acute Toxicity A-l
B. Toxicity of Selenium to Aquatic Plants B-l
C. Bioconcentration and Bioaccumulation of Selenium C-l
D. Environmental Factors Affecting Selenium Toxicity and Bioaccumulation D-l
E. Site-specific Considerations E-l
F. Other Data F-l
G. Unused Data G-l
H. Data Used in Regression Analysis of Selenium in Whole-body Fish Tissue with Selenium in
Muscle, Ovary and Liver Tissue H-l
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I. Summaries of Chronic Studies Considered for FCV Derivation 1-1
J. Selenium in Fish Samples Collected From 112 Sites as Part of U.S. Fish and Wildlife's National
Biomonitoring Program, 1979-1981 J-l
List of Tables
Table A. Particulate and dissolved selenium 7
Table la. Acute Toxicity of Selenium to Freshwater Animals 26
Table Ib. Acute Toxicity of Selenium to Saltwater Animals 40
Table 2a. Ranked Freshwater Genus Mean Acute Values 43
Table 2b. Ranked Saltwater Genus Mean Acute Values 47
Table 3a. Ratios of Freshwater Species Mean Acute Values for Se 49
Table 3b. Ratios of Saltwater Species Mean Acute Values for Sel 51
Table 4. Freshwater Chronic Values from Acceptable Tests 78
List of Figures
Figure 1. Ranked summary of selenite GMAVs (freshwater) 52
Figure 2. Ranked summary of selenate GMAVs (saltwater) 53
Figure 3. Ranked summary of selenate GMAVs (freshwater) at a sulfate level of 100 mg/L 54
Figure 4. The quantile regression curves project median selenium concentrations in the whole
body of bluegill, largemouth bass, tilapia and carp as a function of selenium
concentrations in their tissues 57
Figure 5. Reductions in survival, growth or other responses of organisms are often modeled
as a sigmoid function of increasing concentrations of selenium, or any other toxic
substance 59
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Introduction
This document provides guidance to States and Tribes authorized to establish water quality standards
under the Clean Water Act (CWA) to protect aquatic life from toxic effects of selenium. Under the
CWA, States and Tribes are to establish water quality standards to protect designated uses. While this
document constitutes the U.S. Environmental Protection Agency's (U.S. EPA) scientific
recommendations regarding ambient concentrations of selenium, this document does not substitute for
the CWA or U.S. EPA's regulations; nor is it a regulation itself. Thus, it cannot impose legally binding
requirements on the U.S. EPA, States, Tribes or the regulated community, and might not apply to a
particular situation based upon the circumstances. Interested parties are free to raise questions and
objections about the substance of this guidance and the appropriateness of the application of this
guidance to a particular situation. State and Tribal decision-makers retain the discretion to adopt
approaches on a case-by-case basis that differ from this guidance when appropriate. The U.S. EPA may
change this guidance in the future.
This document establishes water quality criteria for protection of aquatic life for selenium. Under
Section 304(a) of the CWA, U.S. EPA is to periodically revise water quality criteria to accurately reflect
the latest scientific knowledge. Toward this end, a U.S. EPA-sponsored Peer Consultation Workshop on
Selenium Aquatic Toxicity and Bioaccumulation on May 27-28, 1998 brought together experts in
selenium research to discuss issues related to the chronic criterion for selenium. As a result of findings
from the workshop and the fact that a substantial body of literature on the chronic toxicity of selenium
has accumulated since the 1987 document was published, U.S. EPA has decided to update the acute and
chronic criteria for selenium.
The criteria presented herein supersede all previous national aquatic life water quality criteria for
selenium (U.S. EPA 1976, 1980a, 1987a, 1995).
Selenium Chemistry
Water quality criteria are being derived for total selenium measured as selenite-Se plus selenate-Se, but a
variety of forms of selenium can occur in water and tissue. Selenium in aquatic ecosystems exists in a
broad range of oxidation states: (+ VI) in selenates (HSeO4", SeO42") and selenic acid (H2SeO4), (+ IV) in
selenites (HSeO3", SeO32") and selenousacid (H2SeO3), 0 in elemental selenium, and (-II) in selenides
(Se2", HSe"), hydrogen selenide (H2Se), and organic selenides (R2Se). Selenium also shows some
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tendency to form catenated species like organic diselenides (RseSeR). Within the normal physiological
pH range and the reduction potential range permitted by water, only Se, SeO32", HSeO3", and SeO42" can
exist at thermodynamic equilibrium (Mine 1998). While ionic reactions are expected to be rapid in
water, oxidation-reduction reactions may be slow, and the possibility exists for the formation of HSe" in
living systems and some environments where anoxic conditions arise. The parallel behavior of
comparable species of sulfur and selenium in living systems has often been observed, but it is important
to recognize that their chemical characteristics are different in many ways. For instance, selenate is
comparable to chromate in oxidizing strength and far stronger than sulfate [£1°(SeO42"/H2SeO3) = 1.15V;
E°(Cr2O72YCr3+) = 1.33V;E°(SO42-/H2SO3) = 0.200V (standard potentials in acid solution: Weast 1969)],
whereas selenide is a much stronger reducing agent than sulfide [£°(Se/H2Se) = -0.36V; E^S/HjS ]=
0.14V)].
Inorganic Selenium
Selenate usually predominates in well-aerated surface waters, especially those with alkaline conditions.
In spite of its oxidizing strength, selenate (SeO42") exhibits considerable kinetic stability in the presence
of reducing agents (Cotton and Wilkinson 1988). The radius of SeO42" is comparable to that of SO42"
(Frausto da Silva and Williams 1991), and uptake by cells is expected to take place via the same ion
channels or permeases for both anions. Competition between sulfate and selenate uptake has been
observed in many species: algae (Riedel and Sanders 1996), aquatic plants (Bailey et al., 1995), Crustacea
(Olge and Knight 1996), fungi (Gharieb et al. 1995), HeLa cells (Van and Frenkel 1994), and wheat
(Richter and Bergmann 1993). Reduced selenate bioconcentration with increasing sulfate concentration
has been demonstrated inDaphnia magna (Hansen et al. 1993). A significant relationship was shown to
exist between acute selenate toxicity to aquatic organisms and ambient sulfate concentrations (Brix et al.
200la). Competition with selenate has also been observed for phosphate in green algae (Riedel and
Sanders 1996), and with chromate and tungstate in anaerobic bacteria (Oremlandet al. 1989).
Selenous acid species (HSeO3" and SeO32") can predominate in solution under the moderately oxidizing
conditions encountered in oxygenated waters. Between pH 3.5 and 9.0biselenite ion is the predominant
ion in water, and at pH values below 7.0, selenites are rapidly reduced to elemental selenium under
mildly reducing conditions (Faust 1981), situations that are common in bottom sediments.
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Most selenite salts are less soluble than the corresponding selenates. The extremely low solubility of
ferric selenite Fe2(SeO3)3 (Ks= 2.0 ± 1.7 x 10'31), and of the basic ferric selenite Fe2(OH)4SeO3
(Ks = 10"617), is important to the environmental cycling of selenium. Selenites also form stable
adsorption complexes with ferric oxides, forming complexes of even lower solubility than the ferric
selenites. Under certain conditions, selenite (in contrast to selenate) seems to be completely adsorbed in
high amounts by ferric hydroxide and, to a lesser extent, by aluminum hydroxide (Faust 1981).
Coprecipitation techniques have been applied for preconcentration of selenium in natural waters, using
iron (III) hydroxides, which coprecipitates selectively the selenite, but not the selenate, species in river
and sea waters (Yoshii et al. 1977). Alum and iron coagulation precipitation can be used in water
treatment processes to remove selenite (Clifford et al. 1986). The low levels of selenium in ocean waters
have been attributed to the adsorption of selenite by the oxides of metals, such as iron and manganese
(National Academy of Sciences 1976).
Relative to selenate, selenite is more reactive because of its polar character, resulting from the
asymmetric electron density of the ion, its basicity (attraction to bond with proton), and its
nucleophilicity (attraction to bond to a nucleus using the lone pair electrons of the ion). No evidence has
yet been presented to show that HSeO3" or SeO32" is taken up intact into the cell interior. Evidence
indicates that selenite is reduced rapidly, even before uptake in some cases, making it difficult to
distinguish between uptake and metabolic processes (Milne 1998). Freshwater phytoplankton process
selenate and selenite by different mechanisms, leading to different concentrations within the cell, and the
concentrations attained are affected by various chemical and biological factors in the environment
(Riedel et al. 1991). These authors suggested that selenate is transported into the cell by a biological
process with low affinity, whereas selenite appears to be largely physically adsorbed. Contradictory
evidence suggesting that selenite uptake is enzymatically mediated was found with marine phytoplankton
(Baines and Fisher 2001). Experimental results supporting the hypothesis that separate accumulation
mechanisms for selenate and selenite are present in D. magna have been published (Maier et al. 1993).
However, while some organisms appear to absorb selenite nonspecific ally, specific transport systems
exist in other species. Sulfate competition is insignificant in Ruppia maritima (Bailey et al. 1995), and
specific uptake systems have been demonstrated in some microorganisms (Ffeider and Boeck 1993).
Selenite uptake in green algae, unlike selenate, is increased substantially at lower pH values, a property
that represents another difference between these two anions (Riedel and Sanders 1996). The uptake of
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inorganic selenium species, selenate andselenite, by the green algaChlamydomonas reinhardtii (Dang)
was examined as a function of pH over the range 5 to 9, and in media with varying concentrations of
major ions and nutrients using 75Se as a radiotracer. Little difference was noted in the uptake of selenate
as a function of pH, with the maximum uptake found at pH 8; however, selenite uptake increased
substantially at the lower pH values. Differences in speciation are suggested to be the cause of these
differences. Selenate exists as the divalent ion SeO42" over the range of pH tested; whereas monovalent
biselenite ion HSeO3" is prevelant at these pH values. At the low end of the pH range, neutral selenous
acid may also play a role.
Elemental selenium is not measurably soluble in water. It has been reported that elemental selenium is
slowly metabolized by several bacteria (Bacon and Ingledew 1989), and the translocation of elemental
selenium into the soft tissue ofMacoma balthica has been reported (Luoma et al. 1992). The
bioavailability of elemental selenium to M balthica was assessed by feeding the organisms 75Se-labeled
sediments in which the elemental selenium was precipitated by microbial dissimilatory reduction. A
22% absorption efficiency of particulate elemental selenium was observed. In view of the insolubility of
elemental selenium, uptake may be preceeded by air oxidation, or in reducing environments thiols may
facilitate the solubilization (Amaratunga and Milne 1994). Elemental selenium can be the dominant
fraction in sediments (Zawislanski and McGrath 1998).
Selenium is reduced to hydrogen selenide, H2Se, or other selenides at relatively lowredox potentials.
Hydrogen selenide by itself is not expected to exist in the aquatic environment since the Se°/H2Se couple
falls even below the H+/H2 couple. Aqueous solutions of H2Se are actually unstable in air due to its
decomposition into elemental selenium and water. Under moderately reducing conditions, heavy metals
are precipitated as the selenides, which have extremely low solubilities. The following are log Ks values
of some heavy metal selenides of environmental interest: -11.5 (Mn2+), -26.0 (Fe2+), -60.8 (Cu+), -48.1
(Cu2+), -29.4 (Zn2+), -35.2 (Cd2+), and -64.5 (Hg2+). The precipitation of selenium as heavy metal
selenides can be an important factor affecting the cycling of the element in soils and natural waters.
Organoselenium
Organic selenides (conventionally treated as Se(-II) species) in variable concentrations, usually in the
form of free and combined selenomethionine and selenocysteine, are also present in natural surface
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waters (Fisher and Reinfelder 1991). Dissolved organic selenides may be an important source of
selenium for phytoplankton cells, because they can account for -80% of the dissolved selenium in open
ocean surface waters, and for a significant fraction in many other environments as well (Cutter 1989;
Cutter and Cutter 1995). Dissolved organoselenium levels of 142%, 65% and 66% were measured in
samples (one meter depth) fromHyco Reservoir, NC; Robinson Impoundment, SC; and Catfish Lake,
NC; respectively (Cutter 1986). The Hyco Reservoir organoselenium was identified as being protein
bound. Organoselenium concentrations were found to range from 10.4% (58.7 (ig/L) to 53.7% (1.02
(ig/L) of the total selenium present in Lake Creek and Benton Lake, MT surface waters (Zhang and
Moore 1996). Organoselenium quite often is measured as the difference between total dissolved selenium
and the sum of selenite plus selenate, and is therefore not typically characterized. Much more work is
needed in the area of specific identification and characterization of the nature of the organic selenides
present in aquatic ecosystems. Organoselenium form(s) are much more bioavailable and probably play a
very important role in selenium ecotoxic effects (e.g. Besser etal., 1993; Rosetta and Knight 1995).
Departure from Thermodynamic Equilibrium
In the highly dynamic natural waters, there is often a departure from thermodynamic equilibrium. In the
thermodymanic models, kinetic barriers to equilibrium and biological processes are not adequately
considered, and the speciation of selenium in oxidized natural waters is not accurately predicted.
Selenate is usually the predominate form in solution; however, selenite and organoselenium can both
exist at concentrations higher than predicted (Faust 1981; Luoma et al. 1992). Bioaccumulation by
microorganisms, bioproduction and release of organoselenium, and mineralization of particulate
selenium forms contribute to the disequilibrium.
Physical Distribution of Species in Surface Water
The physical distribution of various selenium species in surface waters is regulated by:
• sorption to or incorporation in suspended particulate matter (SPM), and
complexation with inorganic and/or organic colloidal material, such as (FeO 'OH)n and humic
substances (dissolved organic matter, DOM).
Both sorption to SPM and complexation with colloidal matter reduces the bioavailability of the selenium
species. The average fraction of selenium associated with the particulate phase (0.45(im filtration) as
determined from eleven different studies of various surface waters was found to be 16% (0-39% range)
of the total selenium, i.e., an average operationally defined dissolved selenium level of 84% (Text Table
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A). In the James River, VA, the dissolved inorganic and organic selenium was found to be 77% and 70%
associated with colloidal matter, respectively (Takayangi and Wong 1984). A study of lake ecosystems
in Finland (Wang et al. 1995) found that 52% of the dissolved selenium was associated with humic
substances, and in a similar speciation study of Finnish stream waters, Lahermo et al. (1998) determined
that 36% of the selenium was complexed with humic matter. Hence, in various waterbodies physical
distribution as well as chemical speciation of selenium must be considered in relationship to
bioavailability and aquatic toxicity.
Up until recently, the organic selenium fraction has been routinely measured as the difference between
total dissolved selenium and the sum of selenite and selenate. Unfortunately, the calculation of this
important selenium fraction in water as the difference between the total and measurable inorganic
fractions has not permitted this fraction to be fully characterized. New techniques are currently being
developed which should help the specific identification and characterization of the nature of the organic
selenides present in aquatic systems. This work is particularly important because portions of 1he organic
selenium fraction (e.g., selenomethionine) of total dissolved selenium in water have been shown to be
much more bioavailable than the other forms of selenium, and therefore this work is also important for
understanding the manifestation of selenium ecotoxic effects.
Sources of Selenium to Aquatic Systems
Selenium occurs in many soil types and enters ground and surface waters through natural weathering
process such as erosion, leaching and runoff. The national average concentration of selenium in non-
seleniferous surface water ranges from 0.1 to 0.4 (ig Se/L (Maier and Knight 1993). Elevated levels of
selenium occur in surface waters when substantial quantities of selenium enter surface waters from both
natural and anthropogenic sources, ft is abundant in the alkaline soils of North America from the Great
Plains. 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.
Ecological impacts have been observed where selenium is concentrated through irrigation practices in
areas with seleniferous soils. Selenium also occurs in sulfide deposits of copper, lead, mercury, silver
and zinc and can be released during the mining and smelting of these ores. In addition, selenium occurs
naturally in coal and fuel oil and is emitted in flue gas and in fly ash during combustion. Some selenium
then enters surface waters in drainage from fly-ash ponds and in runoff from fly-ash deposits on land.
Notable examples of systems that have been affected by selenium originating from coal ash include
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Belews Lake, NC, where 16 of the 20 species originally present were eliminated within a few years after
discharge began, and Hyco Reservoir, NC, where selenium toxicity was associated with fish larval
mortality (Gillespie and Baumann 1986).
Text Table A. Participate and dissolved selenium as a function of total selenium in freshwater and
marine aquatic ecoystems.
Reference
Cutter 1989
Cutter 1986
Tanizaki et al. 1992
Luomaetal. 1992
Cumbie and VanHorn, 1978
GLEC 1997
Wangetal. 1995
Lahermoetal. 1998
Hamilton et al. 200 lab
Hamilton et al. 2001a,b
Hamilton et al. 2001a,b
Nakamoto and Hassler 1992
Nakamoto and Hassler 1992
Welsh and Maughan 1994
Welsh and Maughan 1994
Welsh and Maughan 1994
Welsh and Maughan 1994
Welsh and Maughan 1994
Welsh and Maughan 1994
Waterbody
Carquinezitist, CA
Hyco Reservoir, NC
Japanese Rivers
San Francisco Bay, CA
Belews Lake, NC
Unnamed Stream, Albright, WV
Finnish Lakes
Finnish Streams
Adobe Creek, Fruita, CO
North Pond, Fruita, CO
Fish Ponds, Fruita, CO
Merced River, CA
Salt Slough, CA
Cibola Lake, CA
Hart Mine Marsh, Blythe, CA
Colorado River, Blythe, CA
Palo Verda Oxbow Lake, CA
Palo Verda Oufall Drain, CA
Pretty Water Lake, CA
Particulate Se
(% of Total)
20-40
0
16
22-31
8
4
10
8
18
0
7
0
4
39
6
11
33
0
21
Fraction
dissolved, fd
0.6-0.8
1
0.84
0.69-0.78
0.92
0.96
0.9
0.92
0.82
1
0.93
1
0.96
0.62
0.94
0.89
0.67
1
0.79
Selenium Biogeochemistry
The current understanding of the biogeochemistry of selenium has recently been reviewed by Fan et al.
(2002). Their review clearly shows the extreme complexity of selenium biogeochemistry in aquatic
environments. Fan et al. describe the selenium biogeochemical cycle as follows: dissolved selenium
oxyanions are primarily absorbed by aquatic producers, including microphytes and bacteria, and
biotransformed into organoselenium form(s) and selenium element (Se°). These, together with other
particle-bound selenium sources, constitute the particulate selenium fraction of the water column, and
they are poorly understood (Zawislanski and McGralh, 1998). Once accumulated in the aquatic primary
and secondary producers, selenium can be transferred through various aquatic consumers (e.g.
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zooplankton, insect larvae, larval fish, bivalves) into the top predators, including aquatic birds and
piscivorous fish. Selenium can be further chemically transformed through the food chain transfer process.
The microscopic planktonic organisms, including microphytes (cyanobacteria and phytoplankton),
bacteria, protozoa, and zooplankton are major components of the particulate matter in the water column.
The particulate matter, in turn, forms the basis for detrital materials which can settle onto the sediment,
and become the food source for sediment organisms. Suspended particulate matter can also be
mineralized in the water column. In addition to 1his selenium input into the sediment, waterborne selenite
and selenate can be physically adsorbed onto the sediment particles, ingested, absorbed, and transformed
by the sediment organisms. Sediment-bound selenate and selenite can be reduced to insoluble Se°by
anaerobic microbial activities. This and water column-derived Se° can be reduced further to inorganic
and organic selenides (-II form), and/or reoxidizedto selenite and selenate by microorganisms in the
sediment and/or in the digestive tracts of sediment macroinvertebrates. Selenides can enter the food chain
via absorption and/or ingestion (by chironomids or tubificid worms, for example) into sediment
organisms, or be oxidized to selenite and selenate. Selenium of different oxidation states can be further
biotransformed by sediment organisms and transferred up the food chain. Selenium biotransformation,
bioaccumulation, and transfer through both sediment and water column foodwebs constitute the major
biogeochemical pathways in aquatic ecosystems.
In addition to accumulating selenium into the biomass, the aquatic producers are the main factors
controlling the volatilization of selenium via the production of methylated selenides including,
dimethylselenide (DMSe) and dimethyldiselenide (DMDSe). These methylated selenides can be oxidized
to selenite, or can exit the water column into the atmosphere. Selenium volatilization into 1he atmosphere
may represent an important process responsible for significant loss of selenium in some aquatic systems.
Methylated selenides can also be generated from dissolved selenonium precursor(s) released by aquatic
producers into the water. Moreover, other organoselenium forms can be released into the water by
aquatic producers, and are reoxidized to selenite and/or reabsorbed by aquatic producers.
Narrow Margin Between Sufficiency and Toxicity
Of all the priority and non-priority pollutants, selenium has the narrowest range of what is beneficial for
biota and what is detrimental. Selenium is an essential element required as a mineral cofactor in the
biosynthesis of glutathione peroxidases. All of the classic glutathione peroxidases contain selenium and
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are found to be involved in the catalytic reaction of these many enzymes (Allan 1999). The major
function of the glutathione peroxidases was found to involve the reduction of hydrogen peroxide to water
at the expense of the oxidation of glutathione, the enzyme's cofactor. Aquatic and terrestrial organisms
require 0.5 (ig/g dry weight (dw) of selenium in their diet to sustain metabolic processes, whereas
concentrations of selenium that are only an order of magnitude greater than the required level have been
shown to be toxic to fish. Selenium deficiency has been found to affect humans (U.S. EPA 1987a), sheep
and cattle (U.S. EPA 1987a), deer (Oliver et al. 1990) fish (Thorarinsson et al. 1994; Wang and Lovell
1997; Wilson et al. 1997; U.S. EPA 1987a), aquatic invertebrates (Audas et al. 1995; Caffrey 1989;
Cooney et al. 1992; Cowgill 1987; Cowgill and Milazzo 1989; Elendt 1990; Elendt and Bais 1990;
Harrison et al. 1988; Hyne et al. 1993; Keating and Caffrey 1989; Larsenand Bjerregaard 1995; Lim and
Akiyama 1995; Lindstrom 1991; U.S. EPA 1987a; Winner 1989; Winner and Whitford 1987), and algae
(Doucette et al. 1987; Keller et al. 1987; Price 1987; Price et al. 1987; Thompson and Hosja 1996; U.S.
EPA 1987a; Wehr and Brown 1985).
Selenium has been shown to mitigate the toxic effects of arsenic, cadmium, copper, inorganic and
organic mercury, silver, ofloxacin, methyl paiathion and the herbicide paraquat to biota in both aquatic
and terrestrial environments (Bjerregaard 1988a, b; Cuvin and Furness 1988; Ding et al. 1988; Krizkova
et al. 1996; Malarvizhi and Usharani 1994; Micallef and Tyler 1987; Patel et al. 1988; Paulsson and
Lundbergh 1991; Pelletier 1986b, 1988; Phillips et al. 1987; Ramakrishna et al. 1988; Rouleau et al.
1992; Salte et al. 1988; Siegel et al. 1991; Szilagyi et al. 1993; U.S. EPA 1987a). Seleniumpretreatment
resulted in reduced effects in 128-hr old, but not 6-hr old, embryos ofOryzias latipes from cadmium and
mercury, whereas prior exposure to selenium did not affect the sensitivity of white suckers to cadmium
(U.S. EPA 1987a). In contrast, Birge et al. and Huckabee and Griffith reported that selenium and
mercury acted synergistically in producing toxic effects to fish embryos (U.S. EPA 1987a). Selenium is
reported to reduce the uptake of mercury by some aquatic species (Southworth et al. 1994; U.S. EPA
1987a), to have no effect on uptake of mercury by a mussel, and to increase the uptake of mercury by
mammals and some fish (U.S. EPA 1987a). Selenium augmented accumulation of cadmium in some
tissues of the shore crab, Carcinus maenas (U.S. EPA 1987a). The available data do not show whether
the various inorganic and organic compounds and oxidation states of selenium are equally effective
sources of selenium as atrace nutrient, oras reducing the toxic effects of various pollutants.
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Selenium Document Information
All concentrations reported herein are expressed as selenium, not as the chemical tested. Although
Se(VI) is expected to be the predominant oxidation state at chemical equilibrium in oxygenated alkaline
waters, the rate of conversion of Se(IV) to Se(VI) seems to be slow in most natural waters. Therefore, it
was assumed that when Se(IV) was introduced into stock or test solutions, it would persist as the
predominate state throughout the test, even if no analyses specific for the Se(IV) oxidation state were
performed. Similarly, it was assumed that when Se(VI) was introduced into stock or test solutions, it
would persist as the predominant state throughout the test, even if no analyses specific for Se(VI) were
performed.
An understanding of the "Guidelines for Deriving Numerical National Water Quality Criteria for the
Protection of Aquatic Organisms and Their Uses" (Stephan et al. 1985), hereafter referred to as the
Guidelines, and the response to public comments (U.S. EPA 1985a) is helpful for understanding the
derivation of the acute criteria for selenium. Briefly, the Guidelines procedure involves the following
steps: (1) Acute toxicity test data is gathered from all suitably conducted studies. Data are to be
available for species in a minimum of eight families representing a diverse assemblage of taxa. (2) The
Final Acute Value (FAV) is derived by extrapolation or interpolation to a hypothetical genus more
sensitive than 95 percent of a diverse assemblage of taxa. The FAV, which represents an LC50 or EC50, is
divided by two in order to obtain an acute criterion protective of nearly all individuals in such a genus.
(3) Chronic toxicity test data (longer-term survival, growth, or reproduction) are needed for at least three
taxa. Most often the chronic criterion is set by determining an appropriate acute-chronic ratio (the ratio
of acutely toxic concentrations to the chronically toxic concentrations) and applying that ratio to the FAV
from the previous step. (4) When necessary, the acute and/or chronic criterion may be lowered to protect
critically important species.
The chronic criteria procedure explicitly set forth in the Guidelines (Step 3 above) is not well suited to
bioaccumulative contaminants for which diet is the primary route of aquatic life exposure.
Consequently, that procedure was not used for deriving the chronic criterion for selenium either in the
original 1987 criteria document or in this update. Rather, to accord with other provisions of the
Guidelines, it was necessary to apply what the Guidelines refer to as "appropriate modifications" of the
procedures in order to obtain a criterion "consistent with sound scientific evidence", as will be described
in a later section.
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Results of such intermediate calculations as recalculated LC50 values 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 latest comprehensive literature search for information for this document was
conducted in August 2001; some more recent information was included.
The body of this document contains only the information on acute and chronic toxicity of selenium that is
relevant to the derivation of the acute and chronic criteria. Supporting information on the toxicity and
bioaccumulation of selenium, and the data that were reviewed and not used in deriving the criteria are
provided in appendices and include: sulfate correction of selenate acute toxicity (Appendix A); toxicity
to aquatic plants (Appendix B); bioconcentration and bioaccumulation (Appendix C); environmental
factors affecting selenium toxicity and bioaccumulation (Appendix D); site-specific considerations
(Appendix E); other data (Appendix F); unused data (Appendix G); tissue relationships (Appendix H);
chronic data summaries (Appendix I); and background Se levels (Appendix!).
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Acute Toxicity of Selenite
Data that may be used, according to the Guidelines, in the derivation of Final Acute Values for selenite
are presented in Tables la and Ib. The following text presents a brief overview of the acceptable data
obtained for selenite, followed by a discussion of the more sensitive, and commercially and
recreationally important species. A ranking of the relative sensitivity of selenite to selenate for each
genera is listed in Tables 2a and 2b.
Acute Toxicity of Se(IV) to Freshwater Animals
Acceptable data on the acute effects of selenite in freshwater are available for 14 species of invertebrates
and 20 species offish (Table la). These 34 species satisfy the eight family provision specified in the
Guidelines. Invertebrates are both the most sensitive and the most tolerant freshwater species to selenite
with Species Mean Acute Values (SMAV) ranging from 440 (ig/L for the crustacean, Ceriodaphnia
dubia, to 203,000 (ig/L for the leech, Nephelopsis obscura. The selenite SMAVs for fishes range from
1,783 (ig/L for the striped bass,Morone saxatilis, to 35,000 (ig/L for the common carp, Cyprinus carpio.
The folio wing text presents aspecies-by-species discussion of the eight most sensitive genera, plus all
commercially and recreationally important species.
Hyalella (amphipod)
The most sensitive freshwater genus is the amphipod, Hyalella, with a Genus Mean Acute Value
(GMAV) of 461.4 (ig Se/L. The GMAV is derived from five 96-hr acute flow-through measured tests
where the LC50 values ranged from 340 to 670 ng Se/L (GLEC 1998; Halter et al. 1980). A sixth test
conducted under non flow-through conditions is also listed in Table la (Brasher and Ogle 1993), but the
Guidelines recommend using flow-through measured data in preference to static or renewal data.
Ceriodaphnia (cladoceran)
The second most sensitive freshwater genus is Ceriodaphnia, with a GMAV of <515.3 (ig Se/L that is
derived from the geometric mean of the C. affinis (<603.6 (ig Se/L) and C. dubia (440 (ig Se/L) SMAVs.
Four static unmeasured 48-hr studies are available for C. affinis where the LC50 values ranged from <480
to 720 (ig Se/L (Owsley 1984; Owsley and McCauley 1986). The one available C. dubia acute study was
conducted by GLEC (1999) that exposed <24-hr old neonates to sodium selenite for 48 hours under flow-
through measured conditions. The resultant 48-hr LC50 value was 440 (ig Se/L, which is the most
sensitive SMAV for selenite in the database.
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Daphnia (cladoceran)
The eleven available acute values are used to calculate the Daphnia magna SMAV of 905.3 (ig Se/L
(acute LC50 values ranged from 215 to 3,020 (ig Se/L), but only one flow-through measured acute LC50
test value of 1,987 (ig Se/L is used for 1he for D. pulex SMAV (a second static measured test conducted
by Reading (1979) is listed, but not used to calculate the SMAV) . The resultant GMAV of 1,341 jig
Se/L for Daphnia is the third most sensitive for selenite.
Hydra
The fourth most sensitive freshwater genus is Hydra, with a GMAV of 1,700 (ig Se/L. The GMAV is
derived from the one available static-measured test conducted by Brooke et al. (1985).
Morone (striped bass)
Two 96-hr static unmeasured tests are available for the striped bass,Morone saxatilis, and the LC50
values were 1,325 and 2,400 (ig Se/L (Palawski et al. 1985). The geometric mean of the two values yield
the GMAV of 1,783 ng Se/L.
Pimephales (fathead minnow)
A total of 16 fathead minnow acute studies are presented in Table la, but only the eight flow-through
measured LC50 values are used to derive the GMAV of 2,209 (ig Se/L. The eight flow-through LC50
values ranged from 620to 5,200 (ig Se/L (Cardwell et al. 1976a,b; GLEC 1998; Kimball manuscript).
Gammarus (amphipod)
The seventh most sensitive freshwater genus is Gammarus, with a GMAV of 3,489 (ig Se/L that is
derived from the geometric mean of five flow-through measured studies (GLEC 1998, 1999) where the
LC50 values ranged from 1,800 to 10,950 (ig Se/L. Two static measured acute studies were conduced by
Brooke et al. (1985) and Brooke (1987), but as recommended by the Guidelines, were not used to
calculate the SMAV for this species.
Jordanella (flagfish)
The eighth most sensitive freshwater genus is Jordanella, with a GMAV of 6,500 (ig Se/L. The GMAV
is derived from the one available 96-hr flow-through measured test conducted by Cardwell et al.
(1976a,b) that exposed Jordanellafloridae to selenium dioxide.
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Oncorhynchus (salmonid)
The GMAV of 10,580 (ig Se/L for the commercially important salmonid Oncorhynchus is derived from
the geometric mean of the coho salmon (O. kisutch; 7,240 (ig Se/L), chinook salmon (O. tshawytscha;
15,596 (ig Se/L) and rainbow trout (O. mykiss; 10,488 (ig Se/L) SMAVs. Three static unmeasured 96-hr
studies are used to calculate the coho salmon SMAV where the LC50 values ranged from 3,578 to 13,600
(ig Se/L (Hamilton and Buhl 1990b; Buhl and Hamilton 1991). A fourth coho salmon LC50 value is
available for an acute test initiated with the tolerant alevin life stage (Buhl and Hamilton 1991), but
based on Guideline recommendations this value is not used when data are available from a more sensitive
life stage.
Six acute chinook salmon static unmeasured 96-hr acute studies conducted wilh the more sensitive post-
alevin life stage of the fish are used to determine the 15,596 (ig Se/L SMAV for the species and the LC50
values ranged from 8,150to 23,400 (ig Se/L (Hamiltonand Buhl 1990b). The two acute studies
conducted with the tolerant eyed egg and alevin life stages by the same authors are not used in the
SMAV determination as recommended by the Guidelines. Hamilton and Buhl (1990b) noted that
chinook salmon fry were consistently more sensitive than eitherthe embryos or alevin to selenite.
A total of seven rainbow trout acute studies are presented in Table la, but only the two flow-through
measured LC50 values are used to derive the SMAV of 10,488 (ig Se/L as recommended by the
Guidelines. The two 96-hr flow-through test LC50 values are 8,800 and 12,500 (ig Se/L (Goettl and
Davies 1976; Hodson et al. 1980). As with the coho and chinook salmon, the alevin life stage was less
sensitive to selenite.
Lepomis (bluegill)
The GMAV of 28,500 (ig Se/L for the recreationally important bluegill sunfish,Lepomis macrochirus, is
derived from the 96-hr flow-through measured test conducted by Cardwellet al. (1976a,b). The static
measured acute study conduced by Brooke et al. (1985) was not used to calculate the SMAV for this
species, as recommended by the Guidelines.
Se(IV) Freshwater Final Acute Value Determination
Freshwater Species Mean Acute Values (Table la) were calculated as geometric means of the available
acute values for selenite, and Genus Mean Acute Values (Table 2a) were then calculated as geometric
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means of the Species Mean Acute Values. Of the 28 genera for which freshwater mean acute values are
available, the most sensitive genus, Hyalella, is 440 times more sensitive than the most tolerant,
Nephelopsis. The range of sensitivities of the four most sensitive genera spans a factor of 3.7. The
freshwater Final Acute Value (FAV), representing the most sensitive 5th percentile genus, is calculated to
be 514.9 (ig/L for selenite using the procedure described in the Guidelines and the Genus Mean Acute
Values in Table 2a. The Final Acute Value is higher than the lowest Species Mean Acute Value (Figure
1).
Acute Toxicity of Se(IV) to Saltwater Animals
Acute toxicity data that can be used to derive a saltwater criterion for selenite are available for 10 species
of invertebrates and eight species offish that are resident in North America (Table Ib). These 18 species
satisfy the eight family provision specified in the Guidelines. The range of SMAVs for saltwater
invertebrates extends from 255 (ig Se/L for juveniles of the bay scallop, Argopecten irradians (Nelson et
al. 1988) to greater than 10,000 (ig Se/L for embryos of the blue mussel, Mytilus edulis (Martin et al.
1981) and embryos of the Pacific oyster, Crassostrea gigas (Glickstein 1978; Martin et al. 1981). The
range of SMAVs for fish is slightly wider than that for invertebrates, extending from 599 (ig Se/L for
larvae of the haddock, Me lanogrammus aeglefmus, to 17,350 (ig Se/L for adults ofthe fourspine
stickleback, Apeltes quadracus (Cardin 1986). No consistent relationship was detected between life
stage of invertebrates or fish and their sensitivity to selenite, and few data are available concerning the
influence of temperature or salinity on the toxicity of selenite to saltwater animals. Acute tests with the
copepod, Acartia tonsa, at 5 and 10°C gave similar results (Lussier 1986). The following text presents a
species-by-species discussion of the eight most sensitive genera, plus all commercially and recreationally
important species. The genera sensitivity ranking is listed in Table 2b.
Argopecten (bay scallop)
The most sensitive saltwater genus is Argopecten, with a GMAV of 255 (ig Se/L. The GMAV is derived
from the one available bay scallop (Argopecten irradians) static-renewal unmeasured test conducted by
Nelson et al. (1988) at a salinity of 25 g/kg.
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Melanogrammus (haddock)
The second most sensitive saltwater genus is Melanogrammus, with a GMAV of 599 (ig Se/L. The
GMAV is derived from the one available haddock (Melanogrammus aeglefinus) static unmeasured test
conducted by Cardin (1986) at a salinity of 30 g/kg.
Cancer (dungeness crab)
The third most sensitive saltwater genus is Cancer, with a GMAV of 1,040 (ig Se/L. The GMAV is
derived from the one available static unmeasured test conducted by Qickstein (1978) that exposed
Cancer magisterto selenium oxide at a salinity of 33.8 g/kg.
Penaeus (brown shrimp)
The fourth most sensitive saltwater genus is Penaeus, with a GMAV of 1,200 (ig Se/L. The GMAV is
derived from the one available static unmeasured test conducted by Wardet al. (1981) that exposed
Penaeus aztecus to sodium selenite at a salinity of 30 g/kg.
Acartia (copepod)
The fifth most sensitive saltwater genus is Acartia, with a GMAV of 1,331 (ig Se/L that is derived from
the geometric mean of the A. clausi (2,110 (ig Se/L) and A tonsa (839 (ig Se/L) SMAVs. Each of the
SMAVs is derived from one static unmeasured acute test conducted by Lussier (1986) that exposed each
species to selenious acid at a salinity of 30 g/kg.
Americamysis (Mysidopsis) (mysid)
The GMAV of 1,500 (ig Se/L for the mysid Americamysis (formerly Mysidopsis) is derived from the one
Americamysis bahia 96-hr flow-through measured test conducted by Ward et al. (1981). The static
unmeasured acute study conduced by U.S. EPA (1978) was not used to calculate 1he SMAV for this
species as recommended by the Guidelines. The flow-through measured test was conducted with
selenious acid at a salinity of 15-20 g/kg.
Spisula (surf clam)
The seventh most sensitive saltwater genus is Spisula, with a GMAV of 1,900 (ig Se/L. The GMAV is
derived from the one available static-renewal unmeasured test conducted by Nelson et al. (1988) that
exposed Spisula solidissima to sodium selenite at a salinity of 25 g/kg.
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Morone (striped bass)
Five 96-hr static unmeasured tests are available for the striped bass, Morone saxatilis, and the LC50
values ranged from l,550to 3,900 (ig Se/L (Chapman 1992; Palawski et al. 1985). The geometric
mean of the five values yielded the GMAV of 3,036 (ig Se/L. All the tests were conducted with sodium
selenite at a salinity of 1 -5 g/kg.
Paralichthys (summer flounder)
The GMAV of 3,497 (ig Se/L for the commercially important summer flounder, Paralichthys dentatus, is
derived from one 96-hr static unmeasured acute test conducted by Cardin (1986) that exposed embryos to
selenious acid at a salinity of 30.2 g/kg.
Callinectes (blue crab)
The GMAV of 4,600 (ig Se/L for the commercially important blue crab, Callinectes sapidus, is derived
from one static unmeasured acute test conducted by Ward et al. (1981) that exposed juveniles to sodium
selenite at a salinity of 30 g/kg.
Crassostrea (Pacific oyster)
Two static unmeasured tests are available forthe commercially important Pacific oyster, Crassostrea
gigas, and the LC50 values were both >10,000 (ig Se/L (Glickstein 1978; Martin et al. 1981). The
geometric mean of the two values yielded the GMAV of >10,000 (ig Se/L. The tests were conducted
with selenium oxide and sodium selenite at a salinity of 33.8 g/kg.
Mytilus (blue mussel)
The GMAV for the commercially important blue mussel, Mytilus edulis, is also > 10,000 (ig Se/L, and is
derived from the one static unmeasured acute test conducted by Martin et al. (1981) that exposed
embryos to selenium oxide at a salinity of 33.8 g/kg.
Pseudopleuronectes (winter flounder)
The GMAV of 14,649 (ig Se/L for the commercially important winter flounder, Pseudopleuronectes
americanus, is derived from two 96-hr static unmeasured acute tests conducted by Cardin (1986) that
exposed larvae to selenious acid at a salinity of 28-30 g/kg.
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Se(IV) Saltwater Final Acute Value Determination
Of the 17 genera for which saltwater mean acute values are available for selenite (Table 2b), the most
sensitive genus, Argopectin, is 68 times more sensitive than the mosttolerant,^4/>e/fe$'. The sensitivities
of the four most sensitive genera differ by a factor of 4.7, and these four include three invertebrates and
one fish, of which an invertebrate is the most sensitive of the four. The saltwater Final Acute Value,
representing the most sensitive 5th percentile genus, is 253.4 (ig/Lfor selenite, which is slightly lower
than the lowest Species Mean Acute Value (Figure 2).
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Acute Toxicity of Selenate
Data that may be used, according to the Guidelines, in the derivation of Final Acute Values for selenate
are presented in Tables la and Ib. The following text presents a brief overview of the acceptable data
obtained for selenate, and includes a discussion of the more sensitive and important species. The genera
sensitivity ranking is listed in Tables 2a and 2b.
Sulfate-dependent Toxicity of Selenate
The toxicity of a number of metals (e.g., copper and cadmium) to aquatic organisms is related to the
concentration of hardness in the water. The toxicity of these metals to many different aquatic species has
been shown to decrease as the hardness concentration increases. A similar relationship also has been
recognized between selenate and dissolved sulfate in freshwater (a similar relationship is not evident
between selenite and sulfate or between either form of selenium and hardness). The studies reviewed in
this document indicate that, as the concentration of sulfate increases, the acute toxicity of selenate is
reduced (less toxic). Selenate acute toxicity tests conducted at different levels of dissolved sulfate are
available with C. dubia, D. magnet, H. azteca, G. pseudolimnaeus, chinook salmon and fathead minnows
(Table la). These data indicate that, in general, selenate is more toxicto these species in low sulfate
water than in higher sulfate water.
Sulfate Correction
As discussed in the introduction of this document, sulfate has been shown to compete with selenate in
their uptake into aquatic organisms (Olge and Knight 1996; Riedel and Sanders 1996; Bailey et al. 1995;
Hansen et al. 1993) and affect the acute toxicity of selenate (Brix et al. 200 la). Sulfate is used here as a
correction to the toxicity of selenate. However, it should be emphasized that the sulfate adjustment is not
a precise measure, but an estimation The variability associated with different life stages, clones and test
conditions of the studies used to determine the sulfate slope all contribute to the uncertainty of the sulfate
correction. In selected cases, insensitive life stages were not used in the analysis (e.g., the eyed-egg and
alevin test results were not used for the chinook salmon).
Following recommendations in the guidelines (Stephan et al. 1985), an analysis of covariance (Sokal and
Rohlf 1981) was implemented in Microsoft Excel to calculate a common slope for regression lines
projecting the natural logarithm of selenate LC50s as a function of the natural logarithm of sulfate
concentrations. The common regression line is the best estimate of the collective relationship between
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toxicity and sulfate concentration. With analysis of covariance, different species will be weighted
relative to the number of data points they have. In this case, the fathead minnow has 18 data points out
of the total of 57, the next most frequent species, C. dubia, has 13 data points, and the four remaining
species have eight or fewer data points.
This analysis of covariance model was fit to the selenate data in Table la for the six species for which
definite acute values ("less than" or "greaterthan" values were not used) were available over a range of
sulfate levels, such that the highest sulfate value was at least three times the lowest, and the highest was
also at least 100 mg/L higher than the lowest (other species in Table la either did not meet these criteria
or did not show any sulfate-toxicity trend due to differences in exposure methods, species, age, etc.). A
list of the species and acute toxicity-sulfate values used to estimate the acute sulfate slope is provided in
Appendix A.
Regression analysis revealed significant, positive slopes for five of six species that had acute values
precisely determined. The slopes for all six species ranged from 0.19 to 0.87, and the common slope for
these six species was 0.5812. An F-test was used to test the null hypothesis that slopes of all species
were equal. This test revealed that the null hypothesis could not be rejected (F5 45 = 2.82, P>0.05).
Individual slopes were not significantly differentthan the overall pooled slope (Tukey test, all |q| <3.3,
q o 05,(2), 47,7 = 4.39). Analysis of covariance thus confirmed that it is correct to assume that there is no
significant variation in slopes among species, and that the overall slope is a reasonable estimate of the
relationship between sulfate concentration and selenate toxicity.
The pooled slope of 0.5 812 was used to adjust the freshwater selenate acute values in Table la to a
sulfate level of 100 mg/L, except where it was not possible because no sulfate value was reported.
Species Mean Acute Values (SMAV) were calculated as geometric means of the adjusted acute values
(only the underlined EC50/LC50 species values were used to calculate the respective SMAV). As stated
in the Guidelines (Stephen et al. 1985), flow-through measured study data are normally given preference
over non-flow-through data for a particular species. In certain cases flow-through measured results were
available, yet preference was given to the sensitive life stage for certain species in calculating SMAVs.
Genus Mean Acute Values (GMAV) at a sulfate level of 100 mg/L were then calculated (Table la) as
geometric means of the available freshwater Species Mean Acute Values and ranted (Table 2a).
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Acute Toxicity of Se(VI) to Freshwater Animals (Sulfate Adjusted Values)
Acceptable data on the acute effects of selenate in freshwater are available for 12 invertebrate species
and 11 species offish (Table la). These 23 species satisfy the eight family provision of the Guidelines.
Invertebrates are both the most sensitive and the most tolerant freshwater species to selenate with sulfate
adjusted SMAVs ranging from 593 (ig/L for the crustacean, Daphnia pulicaria, to 1,515,616 (ig/L for the
leech, Nephelopsis obscura. The selenate SMAVs for fishes range from 10,305 (ig/L for the razorback
sucker, Xyrauchen texanus, to 226,320 (ig/L for channel catfish,Ictaluruspunctatus. The following text
presents a species-by-species discussion of the eight most sensitive genera, plus all commercially and
recreationally important species.
Ceriodaphnia (cladoceran)
The most sensitive freshwater genus is the cladeceran, Ceriodaphnia, with a sulfate adjusted GMAV of
842 (ig Se/L. The GMAV is derived from one 48-hr acute flow-through measured test (GLEC 1999).
Twelve additional tests conducted under non flow-through conditions are also listed in Table la (Brix et
al. 2001a,b), but the Guidelines recommend using flow-through measured data in preference to static or
renewal data.
Hyalella (amphipod)
The second most sensitive freshwater genus is the amphipod, Hyalella, with a sulfate adjusted GMAV of
1,397 (ig Se/L. The GMAV is derived from four 96-hr acute flow-through measured tests where the LC50
values ranged from 723 to 4,224 (ig Se/L (GLEC 1998). Three tests conducted under non flow-through
conditions are also listed in Table la (Adams 1976; Brasher and Ogle 1993; Brix et al. 2001a,b), but are
not used to calculate the SMAV as recommended by the Guidelines.
Daphnia (cladoceran)
The third most sensitive freshwater genus is Daphnia, with a sulfate adjusted GMAV of 1,887 (ig Se/L
that is derived from the geometric mean of the D. magna (3,314 (ig Se/L), D. pulex (3,420 (ig Se/L) and
D. pulicaria (593 (ig Se/L) SMAVs. Five static and one static-renewal measured 48-hr studies are
available forZ). magna where the LC50 values ranged from 1,955 to 5,093 (ig Se/L (Boyum 1984; Brooke
et al. 1985; Dunbar et al. 1983; Ingersol et al. 1990; Maier et al. 1993).
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The D. pulex SMAV of 3,420 (ig Se/L is based on the 48-hr flow-through measured test conducted by
GLEC (1999) that exposed <24-hr old neonates to sodium selenate. Two static measured tests conducted
by Brix et al. (2001a,b), are not used to calculate the SMAV as recommend by the Guidelines.
The one available D. pulicaria acute study was conducted by Boyum (1984) that exposed neonates to
sodium selenate for 48 hours under static measured conditions. The resultant 48-hr LC50 value was 59
(ig Se/L, which is the most sensitive SMAV for selenate in the database.
Gammarus (amphipod)
The fourth most sensitive freshwater genus is Gammarus, with a sulfate adjusted GMAV of 2,522 (ig
Se/L that is derived from the geometric mean of the G. lacustris (2,747 (ig Se/L) and G. pseudolimnaeus
(2,315 (ig Se/L) SMAVs. The static measured acute test conduced by Brix et al. (2001a,b) is the only
LC50 value available for G. lacustris.
The G. pseudolimnaeus SMAV of 2,315 (ig Se/L is based on five 96-hr flow-through measured tests
conducted by GLEC (1998,1999). Two static measured acute studieswere conduced by Brooke et al.
(1985) and Brooke (1987), but as recommended by the Guidelines, were not used to calculate the SMAV
for this species.
Xyrauchen (razorback sucker)
Six 96-hr static unmeasured tests are available for the razorback sucker, Xyrauchen texanus, and the LC50
values ranged from 7,839to 16,184 (ig Se/L (Buhl and Hamilton 1996; Hamilton 1995; Hamilton and
Buhl 1997a). The geometric mean of the six values yield the GMAV of 10,309 (ig Se/L.
Gila (bonytail)
The sixth most sensitive freshwater genus is Gila, with a sulfate adjusted GMAV of 10,560 (ig Se/L.
The GMAV is derived from the one static-unmeasured test conducted with the more sensitive larval stage
(Buhl and Hamilton 1996). Four other static-unmeasured tests were conducted with less sensitive life
stages, but as recommended by the Guidelines, the results were not used to calculate the SMAV for this
species.
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Pimephales (fathead minnow)
A total of nine fathead minnow acute studies are presented in Table la, but only the five flow-through
measured LC50 values are used to derive the sulfate adj usted GMAV of 11,346 (ig Se/L. The five flow-
through LC50 values ranged from 7,286 to 18,860 (ig Se/L (Spehar 1986; GLEC 1998). The four static
tests are not used to calculate the SMAV as recommended by the Guidelines.
Ptychocheilus (Colorado squawfish)
The eighth most sensitive freshwater genus is Ptychocheilus with a sulfate adjusted GMAV of 18,484 (ig
Se/L. The GMAV is derived from the three static-unmeasured test conducted with the sensitive life stage
of Ptychocheilus lucius (Buhl and Hamilton 1996; Hamilton 1995). Three other static-unmeasured tests
were conducted with less sensitive life stages, but as recommended by the Guidelines, the results were
not used to calculate the SMAV for this species.
Oncorhynchus (salmonid)
The sulfate adjusted GMAV of 47,164 (ig Se/L forthe commercially important salmonid Oncorhynchus
is derived from the geometric mean of the coho salmon (O. kisutch; 29,141 (ig Se/L), chinook salmon (O.
tshawytscha; 83,353 (ig Se/L) and rainbow trout (O. mykiss; 43,192 (ig Se/L) SMAVs. Three static
unmeasured 96-hr studies are used to calculate the coho salmon SMAV where the LC50 values ranged
from 20,963 to 51,935 (ig Se/L (Buhl and Hamilton 1991; Hamilton and Buhl 1990b). A fourth coho
salmon LC50 value is available for an acute test initiated with the tolerant alevin life stage (Buhl and
Hamilton 1991), but based on Guideline recommendations this value is not used when data are available
from a more sensitive life stage.
Five acute chinook salmon static unmeasured 96-hr acute studies conducted with the more sensitive life
stage of the fish are used to determine the sulfate adjusted 83,353 (ig Se/L SMAV forthe species wilh
LC50 values ranging from 69,939 to 97,550 (ig Se/L (Hamilton and Buhl 1990b). The two acute studies
conducted with the tolerant eyed egg and alevin life stages by the same authors are not used in the
SMAV determination as recommended by the Guidelines.
A total of four rainbow trout acute studies are presented in Table la, but only the results from the two
static tests conducted with the sensitive juvenile life stage were used to calculate the SMAV of 43,192
(ig Se/L (Brooke et al. 1985; Buhl and Hamilton 1991). The two test results obtained with less sensitive
life stages were not used as recommended by the Guidelines.
23 Draft November 12, 2004
-------
Lepomis (bluegill)
The sulfate adjusted GMAV of 216,033 (ig Se/L for the recreationally important bluegill sunfish,
Lepomis macrochirus, is derived from the 96-hr static measured test conducted by Brooke et al. (1985)
that exposed juvenile bluegill to sodium selenate.
Ictalurus (channel catfish)
The sulfate adjusted GMAV of 226,320 (ig Se/L for the commercially important channel catfish,
Ictalurus punctatus, is derived from the 96-hr static measured test conducted by Brooke et al. (1985) that
exposed juvenile catfish to sodium selenate.
Se(VI) Freshwater Final Acute Value Determination
Of the 18 freshwater genera for which mean sulfate adjusted acute values are available for selenate, the
most sensitive, Ceriodaphnia, is 1,800 times more sensitive than the most tolerant, Nephelopsis. The
range of sensitivities of the four most sensitive genera, all invertebrates, spans a factor of 3.0.
At a sulfate level of 100 mg/L, the freshwater Final Acute Value, representing the most sensitive 5th
percentile genus, was calculated to be 834.4 (ig/L for selenate. This Final Acute Value is lower than the
acute value of the most sensitive freshwater species (Table 2a and Figure 3). The resultant freshwater
Criterion Maximum Concentration (CMC) for selenate (in (ig/L) = e(° 58i2[in(SUFate)]+3 357) At a gulfate
level of 100 mg/L this yields 417.2 (ig/L, or one-half the FAV.
Acute Toxicity of Se(VI) to Saltwater Animals
The only species with which acute tests have been conducted on selenate in salt water is the striped bass
(Table Ib). Klauda (1985a, b) obtained 964ir selenate LC50 values of 9,790 and 85,840 (ig/L using flow-
through measured methodology wilh prolarvae and juvenile striped bass, respectively. In static
unmeasured tests, Chapman (1992) determined selenate 96-hr LC50 values that ranged from 23,700 to
29,000 (ig/L using 24 to 32 day posthatch striped bass larvae. The more sensitive prolarvae life stage test
conducted under flow-through conditions is used to yield the SMAV and GMAV of 9,790 (ig Se/L for
the striped bass.
Se(VI) Saltwater Final Acute Value Determination
The one saltwater species available for selenate does not satisfy the eight family provision specified in
the Guidelines. Therefore, a saltwater Final Acute Value for selenate cannot be determined.
24 Draft November 12, 2004
-------
Comparison of Selenite and Sdenate Acute Toxicity
Species Mean Acute Values have been determined for both selenite and selenate with 20 freshwater
species (Table 3a) and one saltwater species (Table 3b). Of these 21 species, 20 are more sensitive to
Se(IV). Only the amphipod, Gammarus pseudolimnaeus, is more sensitive to Se (VI), and is in the
sensitive portion of the Table 3a distribution. Consistent with the acute toxicity sensitivity pattern, the
FAV for Se(VI) is higher than the FAV for Se (IV).
25 Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals
Species
Hydra (adult),
Hydra sp.
Worm,
Tubifex tubifex
Leech (adult),
Nephelopsis obscura
Snail (adult),
Aplexa hypnorum
Snail (adult),
Aplexa hypnorum
Snail,
Physa sp.
Cladoceran (<24 hr),
Ceriodaphnia dubia
Cladoceran (<24 hr),
Ceriodaphnia affinis
Cladoceran (36-60 hr),
Ceriodaphnia affinis
Cladoceran (84-108 hr),
Ceriodaphnia affinis
Cladoceran (72-120 hr),
Ceriodaphnia affinis
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Method'
S,M
R,U
S,M
S,M
S,M
S,U
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,M
S,M
S,U
S,U
S,U
Chemical
FRES
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acidc
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCCXj
HWATER SPEC
Selenite
-
245
49.8
50.6
49.8
45.7
127
(sulfate=25)
100.8
100.8
100.8
100.8
214
72
129.5
138
-
40
280
LC50
orECSO
IBS
1.700
7.710
203.000
53.000
23.000
24.100
440
600
720
640
<480
2.500
430
1.100
450
215
870
2.370
Species Mean
Acute Value
(ug/L) Reference
1,700 Brooke etal. 1985
7,710 Khangarot 1991
203,000 Brooke etal. 1985
Brooke etal. 1985
34,914 Brooke etal. 1985
24,100 Reading 1979
440 GLEC 1999
Owsley 1984;
Owsley and
McCauley 1986
Owsley 1984
Owsley 1984
<603.6 Owsley 1984
Bringmann and
Kuhnl959a
LeBlanc 1980
Dunbar etal. 1983
Boyum 1984
Adams and
Heidolph 1985
Mayer and
Ellersieck 1986
Mayer and
Ellersieck 1986
26
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran (<24 hr),
Daphnia pulex
Amphipod (adult),
Gammarus
pseudolimnaeus
Amphipod (adult),
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod (adult),
Gammarus
pseudolimnaeus
Amphipod
(2 mm length),
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Method'
S,M
S,M
R, M
S,M
S,M
F,M
S,M
S,M
F,M
F,M
F,M
F,M
F,M
R,M
F,M
F,M
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acid
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCCXl
45.5
136
80-100
220"
46.4
128
(sulfate=25)
48.3
53.6
139
(sulfate=24)
137
(sulfate=138)
144
(sulfate=326)
138
(sulfate=758)
128
(sulfate=25)
133
329
132
(sulfate=64)
LC50
orECSO
700
3.020
550
1.220
3,870
1.987
4,300
1,700
2,260
3.130
1.800
3.710
10.950
420
340
670
Species Mean
Acute Value
(ug/L) Reference
Ingersoll et al.
1990
Ingersoll et al.
1990
Maier etal. 1993
9,05.3 Kimball,
Manuscript
Reading 1979;
Reading and
Buikemal983
1,987 GLEC 1999
Brooke etal. 1985
Brooke 1987
GLEC 1998
GLEC 1998
GLEC 1998
GLEC 1998
3,489 GLEC 1999
Brasher and Ogle
1993
Halter etal. 1980
GLEC 1998
27
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Midge (4th instar),
Chironomus decorus
Midge,
Chironomus plumosus
Midge,
Chironomus plumosus
Midge,
Tanytarsus dissimilis
Coho salmon (0.5 g),
Oncorhynchus kisutch
Coho salmon (2.6 g),
Oncorhynchus kisutch
Coho salmon (alevin),
Oncorhynchus kisutch
Coho salmon (juvenile),
Oncorhynchus kisutch
Chinook salmon (0.7 g),
Oncorhynchus
tshawytscha
Chinook salmon (0.5 g),
Oncorhynchus
tshawytscha
Chinook salmon (1.6 g),
Oncorhynchus
tshawytscha
Chinook salmon (1.6 g),
Oncorhynchus
tshawytscha
Chinook salmon
(eyed egg),
Oncorhynchus
tshawytscha
Chinook salmon (alevin),
Oncorhynchus
Method'
F,M
F,M
F,M
R, M
S,U
S,U
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenium
dioxide
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCCXl
132
(sulfate=138)
138
(sulfate=359)
138
(sulfate=642)
85
39
280
48
211
333
41
41
211
211
333
333
41.7
41.7
LC50
orECSO
<350
<460
570
48.200
24.150
27.850
42.500
7.800
13.600
35,560f
3,578
14.800
13.000
23.100
23.400
>348,320f
64,690f
Species Mean
Acute Value
(ug/L) Reference
GLEC 1998
GLEC 1998
461.4 GLEC 1998
48,200 Maier and Knight
1993
Mayer and
Ellersieck 1986
25,934 Mayer and
Ellersieck 1986
42,500 Call etal. 1983
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Buhl and
Hamilton 1991
7,240 Buhl and
Hamilton 1991
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
tshawytscha
28
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Chinook salmon (0.31 g),
Oncorhynchus
tshawytscha
Chinook salmon (0.46 g),
Oncorhynchus
tshawytscha
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout
(alevin),
Oncorhynchus mykiss
Rainbow trout
(juvenile),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Brook trout
(adult),
Salvelinus fontinalis
Arctic grayling
(alevin),
Thymallus arcticus
Arctic grayling
(juvenile),
Thymallus arcticus
Goldfish,
Carassius auratus
Common carp,
Cyprinus carpio
Golden shiner,
Notemigonus crysoleucas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Method'
S,U
S,U
S,U
S,U
S,U
S,U
S,U
F,M
F,M
F,M
S,U
S,U
F,M
R,U
F,M
S,U
S,U
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenium
dioxide
Sodium
selenite
Sodium
selenite
Selenium
dioxide
-
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCCXl
41.7
41.7
330
330
272
41
41
30
135
157
41
41
157
-
72.2
312
(13°C)
312
(13°C)
LC50
orECSO
16.980
8.150
4,500
4,200
1,800
118,000
9,000
12,500
8.800
10.200
34,732f
15.675
26.100
35.000
11.200
10,500
11,300
Species Mean
Acute Value
Cue/Li
-
15,596
_
-
_
_
.
10,488
10,200
-
15,675
26,100
35,000
11,200
_
Reference
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Adams 1976
Adams 1976
Hunnetal. 1987
Buhl and
Hamilton 1991
Buhl and
Hamilton 1991
Goettl and Davies
1976
Hodsonetal. 1980
Cardwell et al.
1976a,b
Buhl and
Hamilton 1991
Buhl and
Hamilton 1991
Cardwell et al.
1976a,b
Satoetal. 1980
Hartwell et al.
1989
Adams 1976
Adams 1976
29
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow
(30 days),
Pimephales promelas
Fathead minnow
(juvenile),
Pimephales promelas
Fathead minnow
(fiy).
Pimephales promelas
Fathead minnow
(juvenile),
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Colorado squawfish
(fry),
Ptychocheilus lucius
Colorado squawfish
(0.4-1.1 g juvenile),
Ptychocheilus lucius
Colorado squawfish
(1.7 g juvenile),
Method'
S,U
S,U
S,U
S,U
S,M
S,U
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
S,U
S,U
S,U
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenium
dioxide
Selenium
dioxide
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acid
Selenious
acid
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCCXl
303
(20°C)
303
(20°C)
292
(25°C)
292
(25°C)
51.1
40
157
157
131
(sulfate=24)
131
(sulfate=160)
145
(sulfate=214)
140
(sulfate=870)
220"
220"
197
197
197
LC50
orECSO
(fig/L^
6,000
7,400
3,400
2,200
1,700
7,760
2,100
5.200
3.670
2.920
3.390
2.380
620
970
6.398
16.452
14.624
Species Mean
Acute Value
(ug/L) Reference
Adams 1976
Adams 1976
Adams 1976
Adams 1976
Brooke etal. 1985
Mayer and
Ellersieck 1986
Cardwell et al.
1976a,b
Cardwell et al.
1976a,b
GLEC 1998
GLEC 1998
GLEC 1998
GLEC 1998
Kimball,
Manuscript
2,209 Kimball,
Manuscript
Hamilton 1995
Hamilton 1995
Hamilton 1995
Ptychocheilus lucius
30
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Colorado squawfish
(larva),
Ptychocheilus lucius
Colorado squawfish
(juvenile),
Ptychocheilus lucius
Colorado squawfish
(0.024-0.047 g),
Ptychocheilus lucius
Bonytail (fry),
Gila elegans
Bonytail (1.1 g juvenile),
Gila elegans
Bonytail (2.6 g juvenile),
Gila elegans
Bonytail (larva),
Gila elegans
Bonytail (juvenile),
Gila elegans
Razorback sucker
(fry),
Xyrauchen texanus
Razorback sucker
(0.9 g juvenile),
Xyrauchen texanus
Razorback sucker
(2.0 g juvenile),
Xyrauchen texanus
Razorback sucker
(larva),
Xyrauchen texanus
Razorback sucker
(juvenile),
Xyrauchen texanus
Razorback sucker
(0.006-0.042 g),
Xyrauchen texanus
White sucker,
Catostomus commersoni
White sucker,
Catostomus commersoni
Method'
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
s,u
F,M
F, M
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCCXl
199
199
144
197
197
197
199
199
197
197
197
199
199
144
10.2
18
LC50
orECSO
7.960
17.350
20.700
8.680
7.769
6.855
14.490
12.870
6.855
4.067
7.312
10.450
8.520
11.300
29.000
31.400
Species Mean
Acute Value
(ug/L) Reference
Buhl and
Hamilton 1996
Buhl and
Hamilton 1996
12,801 Hamilton and
Buhl 1997a
Hamilton 1995
Hamilton 1995
Hamilton 1995
Buhl and
Hamilton 1996
9,708 Buhl and
Hamilton 1996
Hamilton 1995
Hamilton 1995
Hamilton 1995
Buhl and
Hamilton 1996
Buhl and
Hamilton 1996
7,679 Hamilton and
Buhl 1997a
Klaverkamp et al.
1983a
30,176 Duncan and
Klaverkamp 1983
31
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species Method' Chemical
Flannelmouth sucker S, U Sodium
(12-13 days), selenite
Catostomus latipinnis
Hardness LC50 Species Mean
(mg/L as or EC50 Acute Value
CaCO?l fug/L^ (ug/L) Reference
144 19.100 19,100 Hamilton and
Buhl 1997b
Striped bass (63 days),
Morone saxatilis
S,U
Sodium
selenite
40
1.325
Channel catfish (juvenile), S, M Sodium 49.8 16,000
Ictalurus punctatus selenite
Channel catfish (juvenile), S, U Sodium 41 4,110
Ictalurus punctatus selenite
Channel catfish, F, M Selenium 157 13.600
Ictalurus punctatus dioxide
13,600
Palawski et al.
1985
Striped bass (63 days),
Morone saxatilis
S,U
Sodium
selenite
285
2.400
1,783
Palawski et al.
1985
Brooke etal. 1985
Mayer and
Ellersieck 1986
Cardwell et al.
1976a,b
Flagfish,
Jordanella floridae
F,M
Selenium
dioxide
157
6.500
6,500
Cardwell et al.
1976a,b
Mosquitofish,
Gambusia afjinis
S,U
Sodium
selenite
45.7
12.600
12,600 Reading 1979
Bluegill (juvenile). S, M Sodium 50.5 12,000
Lepomis macrochirus selenite
Bluegill, F,M Selenium 157 28.500
Lepomis macrochirus dioxide
Brooke etal. 1985
28,500 Cardwell et al.
1976a,b
Yellow perch,
Perca flavescens
F,M Sodium 10.2 11.700 11,700 Klaverkamp et al.
selenite 1983a
Species
Method" Chemical
Hardness
(mg/L as
LC50 or EC50 Species Mean
LC50 Adj. To Acute Value at
or EC50 Sulfate = 100 Sulfate = 100
I>g/Ly (ug/L) (ug/L)
FRESHWATER SPECIES
Selenate
Reference
Hydra (adult),
Hydra sp.
S,M
Sodium
selenate
53.6
(sulfate=12)
7300
25.032
25,032
Brooke et al.
1985
Leech (adult),
Nephelopsis
obscura
S,M
Sodium
selenate
49.3
(sulfate=12)
442000
1,515,661
1,515,661
Brooke et al.
1985
Snail,
Aplexa hypnorum
S,M Sodium 51.0 193000
selenate (sulfate=12)
661.816 661,816 Brooke etal.
1985
32
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Hardness
(mg/L as
MethoJ Chemical CaCO.l
LC50 or EC50 Species Mean
LC50 Adj. To Acute Value at
or EC50 Sulfate = 100 Sulfate = 100
rug/L)b (ug/L) fug/Li
Reference
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
S, M Sodium
selenate
52 1967
(sulfate=52)
52 1864
(sulfate=55)
52 1078
(sulfate=31)
52 580
(sulfate=38)
52 1822
(sulfate=98)
52 1728
(sulfate=98)
52 1453
(sulfate=213)
52 2812
(sulfate=217)
52 5553
(sulfate=378)
52 5481
(sulfate=378)
52 9157
(sulfate=926)
2,877
2,638
2,129
1,018
1,844
1,748
936
1,793
2,564
2,531
2,512
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
Brix et al.
2001a,b
33
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
LC50 or EC50 Species Mean
Species
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran
(<24 hr),
Ceriodaphnia
dubia
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia pulex
Cladoceran (<24
hr),
Daphnia pulex
Cladoceran (<24
hr),
Daphnia pulex
Cladoceran,
Daphnia pulicaria
Amphipod(8-12
mm),
Gammarus
lacustris
Amphipod (adult),
Gammarus
pseudolimnaeus
Amphipod (adult),
Gammarus
pseudolimnaeus
Method^
S,M
F,M
S,M
S,M
S,M
S,M
S,M
R,M
S,M
S,M
F,M
S,M
S,M
S,M
S,M
Chemical
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Hardness LC50
(mg/L as or EC50
CaCCXl I>g/Ly
52 9311
(sulfate=1205)
127 376
(sulfate=25)
129.5 5300
(sulfate=163)
138 1010
(sulfate=22)
48.1 570
(sulfate=12)
45.5 2560
(sulfate=41)
136 4070
(sulfate=68)
80-100 2840
(sulfate=82)
52 10123
(sulfate=54)
52 8126
(sulfate=38)
147 1528
(sulfate=25)
138 246
(sulfate=22)
116 3054
(sulfate=120)
46.1 75
(sulfate=12)
51.0 57
(sulfate=12)
Adj. To
Sulfate = 100
(ug/L)
2,191
842
3.990
2,435
1,955
4.298
5.093
3.187
14,482
14,233
3.420
593
2.747
257
196
Acute Value at
Sulfate = 100
(ug/L) Reference
Brix et al.
2001a,b
842 GLEC 1999
Dunbar et al.
1983
Boyum 1984
Brooke et al.
1985
Ingersoll et al.
1990
Ingersoll et al.
1990
3,314 Maieretal. 1993
Brix et al.
2001a,b
Brix et al.
2001a,b
3,420 GLEC 1999
593 Boyum 1984
2,747 Brix et al.
2001a,b
Brooke et al.
1985
Brooke 1987
34
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
LC50 or EC50 Species Mean
Species
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod (adult),
Gammarus
pseudolimnaeus
Amphipod,
Hyalella azteca
Amphipod
(2 mm length),
Hyalella azteca
Amphipod
(7-10 days),
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Midge (4th instar),
Chironomus
decorus
Midge (3rd instar),
Paratany tarsus
parthenogeneticus
Coho salmon
(0.5 g),
Oncorhynchus
kisutch
Method'
F,M
F,M
F,M
F,M
F,M
F,U
R,M
S,M
F,M
F,M
F,M
F,M
R,M
S,M
S,U
Chemical
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Hardness
(mg/L as
CaCO.l
139
(sulfate=25)
132
(sulfate=125)
137
(sulfate=367)
134
(sulfate=635)
131
(sulfate=25)
336.8
(sulfate NA)
133
(sulfate=13)
52
(sulfate=55)
143
(sulfate=40)
132
(sulfate=125)
137
(sulfate=367)
133
(sulfate=822)
85
(sulfate=27)
49.4
(sulfate=12)
211
(sulfate=185)
LC50
or EC50
1180
2870
3710
3270
2191
760
1031
1424
2480
1350
1540
3580
23700
20000
32500
Adj. To
Sulfate = 100
2.641
2,521
1,743
1,167
4,904
--
3,375
2,021
4,224
1.186
723
1.052
50.727
68.582
22.730
Acute Value at
Sulfate = 100
(ug/L) Reference
GLEC 1998
GLEC 1998
GLEC 1998
GLEC 1998
2,315 GLEC 1999
Adams 1976
Brasher and Ogle
1993
Brix et al.
2001a,b
GLEC 1998
GLEC 1998
GLEC 1998
1,397 GLEC 1998
50,727 Maier and Knight
1993
68,582 Brooke et al.
1985
Hamilton and
Buhl 1990b
35
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
Species
Hardness
(mg/L as
Method' Chemical CaCO.l
LC50 or EC50 Species Mean
LC50 Adj. To Acute Value at
or EC50 Sulfate = 100 Sulfate = 100
(ug/L)b (ug/L) (ug/U
Reference
Coho salmon
(1.7 g),
Oncorhynchus
kisutch
Coho salmon
(alevin),
Oncorhynchus
kisutch
Coho salmon
(juvenile),
Oncorhynchus
kisutch
Chinook salmon
(0.7 g),
Oncorhynchus
tshawytscha
Chinook salmon
(0.5 g),
Oncorhynchus
tshawytscha
Chinook salmon
(1.6 g),
Oncorhynchus
tshawytscha
Chinook salmon
(1.6 g),
Oncorhynchus
tshawytscha
Chinook salmon
(eyed egg),
Oncorhynchus
tshawytscha
Chinook salmon
(alevin),
Oncorhynchus
tshawytscha
Chinook salmon
(0.31 g),
Oncorhynchus
tshawytscha
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, U Sodium
selenate
S, M Sodium
selenate
333 39000 20.963
(sulfate=291)
41 158,422f 265,990f
(sulfate=41)
41 30932 51.935
(sulfate=41)
211 121000 84.626
(sulfate=185)
211 100000 69.939
(sulfate=185)
333 180000 96.752
(sulfate=291)
333 134000 72.026
(sulfate=291)
41.7 >552,000f >856,083f
(sulfate=47)
41.7 >176,640f >273,947f
(sulfate=47)
41.7 62900 97,550
(sulfate=47)
51.0 24000 82.298
(sulfate=12)
Hamilton and
Buhl 1990b
Buhl and
Hamilton 1991
29,141 Buhl and
Hamilton 1991
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
Hamilton and
Buhl 1990b
83,353 Hamilton and
Buhl 1990b
Brooke et al.
1985
36
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
LC50 or EC50 Species Mean
Species
Rainbow trout
(alevin),
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Arctic grayling
(alevin),
Thymallus arcticus
Arctic grayling
(juvenile),
Thymallus arcticus
Fathead minnow,
Pimephales
promeles
Fathead minnow,
Pimephales
promeles
Fathead minnow,
Pimephales
promeles
Fathead minnow
(juvenile),
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Method'
S,U
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,M
F,M
F,M
F,M
F,M
Chemical
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Hardness LC50
(mg/L as or EC50
CaCCXl (iis/L)b_
41 196460
(sulfate=41)
45 47000
(sulfate=12)
41 13501
(sulfate=41)
41 41800
(sulfate=41)
41 75240
(sulfate=41)
323 11800
(sulfate NA)
323 11000
(sulfate NA)
323 12500
(sulfate NA)
47.9 2300
(sulfate =12)
46 5500
(sulfate =12)
136 6210
(sulfate=24)
127 10800
(sulfate=160)
131 18000
(sulfate=474)
Adj . To Acute Value at
Sulfate = 100 Sulfate = 100
(ug/L) (ug/L) Reference
329,856f - Buhl and
Hamilton 1991
161,168f - Speharl986
22,668 43,192 Buhl and
Hamilton 1991
70,182 - Buhl and
Hamilton 1991
126,328 94,159 Buhl and
Hamilton 1991
Adams 1976
Adams 1976
Adams 1976
7,887 - Brooke et al.
1985
18,860 - Spehar 1986
14,236 - GLEC 1998
8,218 - GLEC 1998
7,286 - GLEC 1998
37
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
LC50 or EC50 Species Mean
Hardness LC50 Adj. To Acute Value at
(mg/L as or EC50 Sulfate = 100 Sulfate = 100
Species
Fathead minnow,
Pimephales
promelas
Colorado
squawfish
(fry),
Ptychocheilus
lucius
Colorado
squawfish
(0.4-1. Ig
juvenile),
Ptychocheilus
lucius
Colorado
squawfish
(1.7 g juvenile),
Ptychocheilus
lucius
Colorado
squawfish (larva),
Ptychocheilus
lucius
Colorado
squawfish
(0.024-0.047 g),
Ptychocheilus
lucius
Colorado
squawfish
(juvenile),
Ptychocheilus
lucius
Bonytail
(fry),
Gila elegans
Bonytail
(1.1 g juvenile),
Gila elegans
Bonytail
(2.6 g juvenile),
Gila elegans
Bonytail
(juvenile),
Gila elegans
Method'
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
Chemical
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
CaCCXl I>g/Ly (ug/L)
147 42100 11.695
(sulfate=906)
196 27588 20,694
(sulfate=164)
196 119548 89,676f
(sulfate=164)
196 138358 103,786f
(sulfate=164)
199 13580 9,842
(sulfate=174)
144 88000 89,572f
(sulfate=97)
199 42780 31,005
(sulfate=174)
196 22990 17,245f
(sulfate=164)
196 102828 77,134f
(sulfate=164)
196 90706 68,041f
(sulfate=164)
199 24010 17,401f
(sulfate=174)
(ug/L) Reference
11,346 GLEC 1998
Hamilton 1995
Hamilton 1995
Hamilton 1995
Buhl and
Hamilton 1996
Hamilton and
Buhl 1997a
18,484 Buhl and
Hamilton 1996
Hamilton 1995
Hamilton 1995
Hamilton 1995
Buhl and
Hamilton 1996
38
Draft November 12, 2004
-------
Table la. Acute Toxicity of Selenium to Freshwater Animals (continued)
LC50 or EC50 Species Mean
Species
Bonytail
(larva),
Gila elegans
Razorback sucker
(fry),
Xyrauchen texanus
Razorback sucker
(0.9 g juvenile),
Xyrauchen texanus
Razorback sucker
(2.0 g juvenile),
Xyrauchen texanus
Razorback sucker
(larva),
Xyrauchen texanus
Razorback sucker
(juvenile),
Xyrauchen texanus
Razorback sucker
(0.006-0.042 g),
Xyrauchen texanus
Flannelmouth
sucker
(12-13 days),
Catostomus
latipinnis
Channel catfish
(juvenile),
Ictalurus
punctatus
Bluegill (juvenile),
Lepomis
macrochirus
Method'
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,M
S,M
Chemical
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Hardness LC50
(mg/L as or EC50
CaCCXl fug/L^
199 14570
(sulfate=174)
196 20064
(sulfate=164)
196 15048
(sulfate=164)
196 10450
(sulfate=164)
199 13910
(sulfate=174)
199 7620
(sulfate=174)
144 15900
(sulfate=97)
144 26900
(sulfate=97)
51.0 66000
(sulfate=12)
50.4 63000
(sulfate=12)
Adj . To Acute Value at
Sulfate = 100 Sulfate = 100
(ug/L) (us/L) Reference
10,560 10,560 Buhl and
Hamilton 1996
15,051 - Hamilton 1995
11,288 -- Hamilton 1995
7,839 - Hamilton 1995
10,081 - Buhl and
Hamilton 1996
5,523 - Buhl and
Hamilton 1996
16,184 10,309 Hamilton and
Buhl 1997a
27,380 27,380 Hamilton and
Buhl 1997b
226,320 226,320 Brooke et al.
1985
216.033 216,033 Brooke etal.
1985
a S = static; R = renewal; F = flow-through; M
b Concentration of selenium, not the chemical.
= measured; U = unmeasured.
Note: The values underlined in this
column were used to calculate the SMAV
for the respective species.
c Reported by Barrows et al. (1980) in work performed in the same laboratory under the same contract.
"From Smith etal (1976).
e Calculated from regression equation.
f Not used in calculation of Species Mean Acute Value because data are available for a more sensitive life stage.
39
Draft November 12, 2004
-------
Table Ib. Acute Toxicity of Selenium to Saltwater Animals
Species
Blue mussel
(embryo),
Mytilus edulis
Bay scallop
(juvenile),
Argopecten irradians
Pacific oyster
(embryo),
Crassostrea gigas
Pacific oyster
(embryo),
Crassostrea gigas
Surf clam
(juvenile),
Spisula solidissima
Copepod
(adult),
Acartia clausi
Copepod
(adult),
Acartia tonsa
Mysid
(juvenile),
Americamysis bahia
Mysid
(juvenile),
Americamysis bahia
Brown shrimp
(juvenile),
Penaeus aztecus
Dungeness crab
(zoea larva),
Cancer magister
Blue crab
(juvenile),
Callinectes sapidus
Method;;
S,U
R, U
S,U
S,U
R, U
S,U
S,U
S,U
F,M
S,U
S,U
S,U
LC50
Salinity orECSO
Chemical (g/kg) (p.e/L~f_
SALTWATER SPECIES
Selenite
Selenium 33.79
oxide
Sodium 25
selenite
Selenium 33.79
oxide
Sodium 33.79
selenite
Sodium 25
selenite
Selenious 30
acid
Selenious 30
acid
Selenious
acid
Selenious 15-20
acid
Sodium 30
selenite
Selenium 33.79
oxide
Sodium 30
selenite
>10.000
255
>10,000
>10,000
1,900
2.110
839
600
1.500
1.200
1.040
4.600
Species Mean
Acute Value
(ug/L) Reference
>10,000 Martin etal. 1981
255 Nelson etal. 1988
Glickstein 1978;
Martin etal. 1981
>10,000 Glickstein 1978
1,900 Nelson etal. 1988
2,110 Lussierl986
839 Lussierl986
U.S. EPA 1978
1,500 Ward etal. 1981
1,200 Ward etal. 1981
1,040 Glickstein 1978
4,600 Ward etal. 1981
40
Draft November 12, 2004
-------
Table Ib. Acute Toxicity of Selenium to Saltw ater Animals (continued).
Species
Haddock
(larva),
Melanogrammus
aeglefinus
Sheepshead minnow
(juvenile),
Cyrinodon variegatus
Sheepshead minnow
(juvenile),
Cyrinodon variegatus
Atlantic silveiside
(juvenile),
Menidia menidia
Fourspine stickleback
(adult),
Apeltes quadracus
Striped bass,
Morone saxatilis
Striped bass
(24 d posthatch),
Morone saxatilis
Striped bass
(25 d posthatch),
Morone saxatilis
Striped bass
(31 d posthatch),
Morone saxatilis
Striped bass
(32 d posthatch),
Morone saxatilis
Pinfish
(juvenile),
Lagodon rhomboides
Summer flounder
(embryo),
Paralichthys dentatus
Winter flounder
(larva),
Pseudopleuronectes
amencanus
Winter flounder
(larva),
Pseudopleuronectes
americanus
Method;;
S,U
S,U
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
s,u
s,u
Chemical
Selenious
acid
Selenious
acid
Sodium
selenite
Selenious
acid
Selenious
acid
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acid
Selenious
acid
Selenious
acid
Salinity
30
-
30
30
30
1
5
5
5
5
30
30.2
30
28
LC50
orECSO
599
6,700
7,400
9,725
17.350
1.550
3.400
3.300
3.800
3.900
4.400
3.497
14,240
15,070
Species Mean
Acute Value
(US/L)
599
-
7,400
9,725
17,350
-
-
-
-
3,036
4,400
3,497
.
14,649
Reference
Cardin 1986
Heitmuller et al.
1981
Wardetal. 1981
Cardin 1986
Cardin 1986
Palawski et al.
1985
Chapman 1992
Chapman 1992
Chapman 1992
Chapman 1992
Wardetal. 1981
Cardin 1986
Cardin 1986
Cardin 1986
41
Draft November 12, 2004
-------
Table Ib. Acute Toxicity of Selenium to Saltw ater Animals (continued).
Species
Method' Chemical
Salinity
(g/kg)
LC50
orECSO
Species Mean
Acute Value
fug/Li
Reference
Selenate
Striped bass
(24 d posthatch),
Morone saxatilis
Striped bass
(25 d posthatch),
Morone saxatilis
Striped bass
(31 d posthatch),
Morone saxatilis
Striped bass
(32 d posthatch),
Morone saxatilis
Striped bass
(juvenile),
Morone saxatilis
Striped bass
(prolarvae),
Morone saxatilis
S, U Sodium 5
selenate
S, U Sodium 5
selenate
S, U Sodium 5
selenate
S, U Sodium 5
selenate
F, M Sodium 6.0-6.5
selenate
F,M Sodium 3.5-4.2
selenate
26,300° - Chapman 1992
23,700° - Chapman 1992
26,300° - Chapman 1992
29,000° - Chapman 1992
85,840° - Klauda 1985a,b
9,790 9,790 Klauda 1985a,b
a S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
b Concentration of selenium, not the chemical. Note: The values underlined in this column were used to calculate the SMAV
for the respective species.
° Not used in calculation of Species Mean Acute Value because data are available for a more sensitive life stage.
42
Draft November 12, 2004
-------
Table 2a. Ranked Freshwater Genus Mean Acute Values
Number of Acute
.anka
28
27
26
25
24
23
22
21
20
19
18
17
16
15
14
13
Genus Mean
Acute Value
Cue/Li
203,000
42,500
35,356
35,000
34,914
28,500
26,100
24,100
24,008
15,675
13,600
12,801
12,600
11,700
11,200
10,580
Species
FRESHWATER SPECIES
Selenite
Leech,
Nephelopsis obscura
Midge,
Tanyta rsus dissimilis
Midge,
Chironomus decorus
Midge,
Chironomus plumosus
Common carp,
Cyprinu s carpio
Snail,
Aplexa hypnorum
Bluegill,
Lepomis macrochirus
Goldfish,
Carassius auratus
Snail,
Physa sp.
White sucker,
Catostomus commersoni
Flannelmouth sucker
Catostom us latipinn is
Arctic grayling
Thymallus arcticus
Channel catfish,
Ictalurus punctatus
Colorado squawfish,
Ptychocheilus lucias
Mosquito fish,
Gam busia affin is
Yellow perch,
Percaflavescens
Golden shiner,
Notemigonus crysoleucas
Chinook salmon,
Species Mean
Acute Value
(>g/L)b
203,000
42,500
48,200
25,934
35,000
34,914
28,500
26,100
24,100
30,176
19,100
15,675
13,600
12,801
12,600
11,700
11,200
15,596
Values used to
Calculate Species
Mean Value b
1
1
1
2
1
2
1
1
1
2
1
1
1
6
1
1
1
6
Oncorhynchus tshawytscha
43
Draft November 12, 2004
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Table 2a. Ranked Freshwater Genus Mean Acute Values (continued)
Number of Acute
.anka
12
11
10
9
8
7
6
5
4
3
2
1
Genus Mean
Acute Value
(US/L)
10,200
9,708
7,710
7,679
6,500
3,489
2,209
1,783
1,700
1,341
<515.3
461.4
Species
Coho salmon,
Oncorhynchus kisutch
Rainbow trout,
Oncorhynchus mykiss
Brook trout
Salvelinu sfontinalis
Bonytail
Gilas elegans
Worm,
Tubifex tubifex
Razorback sucker,
Xyrauchen texanus
Flagfish,
Jordanella floridae
Amphipod,
Gammarus pseudolimnaeus
Fathead minnow,
Pimephales promekis
Striped bass,
Morone saxatilis
Hydra,
Hydra sp.
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Ceriodaphnia affinis
Cladoceran,
Ceriodaphnia dubia
Amphipod,
Hyalella azteca
Species Mean
Acute Value
(ua/LV3
7,240
10,488
10,200
9,708
7,710
7,679
6,500
3,489
2,209
1,783
1,700
905.3
1,987
<603.6
440
461.4
Values used to
Calculate Species
Mean Valueb
3
2
1
5
1
6
1
5
8
2
1
11
1
4
1
5
44
Draft November 12, 2004
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Table 2a. Ranked Freshwater Genus Mean Acute Values (continued)
Number of Acute
.anka
18
17
16
15
14
13
12
11
10
9
8
7
6
5
4
Genus Mean
Acute Value
(US/L)
1,515,661
661,816
226,320
216,033
94,159
68,582
50,727
47,164
27,380
25,032
18,484
11,346
10,560
10,309
2,522
Species
Selenate
(atsulfate= lOOmg/L)
Leech,
Nephelopsis obscura
Snail,
Aplexa hypnorum
Channel catfish,
Ictalurus punctatus
Bluegill,
Lepomis macrochirus
Arctic grayling,
Thymallus arcticus
Midge,
Paratany tarsus
parthenogeneticus
Midge,
Chironomus decorus
Chinook salmon,
Oncorhynchus tshawytscha
Coho salmon,
Oncorhynchus kisutch
Rainbow trout,
Oncorhynchus mykiss
Flannelmouth sucker
Catostom us latipinn is
Hydra,
Hydra sp.
Colorado squawfish,
Ptychocheilus lucius
Fathead minnow,
Pimephales promehs
Bony tail,
Gila elegans
Razorback sucker,
Xyrauchen texanus
Amphipod,
Gam mams la custris
Amphipod,
Species Mean
Acute Value
(ua/LV3
1,515,661
661,816
226,320
216,033
94,159
68,582
50,727
83,353
29,141
43,192
27,380
25,032
18,484
11,346
10,560
10,309
2,747
2,315
Values used to
Calculate Species
Mean Valueb
1
1
1
1
2
1
1
5
3
2
1
1
3
5
1
6
1
5
Gammarus pseudolimnaeus
45
Draft November 12, 2004
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Table 2a. Ranked Freshwater Genus Mean Acute Values (continued)
Number of Acute
Rank8
3
2
1
Genus Mean
Acute Value
(US/L)
1,887
1,397
842
Species
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Daph nia pulica ria
Amphipod,
Hyalella azteca
Cladoceran,
Ceriodaphnia dubia
Species Mean
Acute Value
(ua/LV3
3,314
3,420
593
1,397
842
Values used to
Calculate Species
Mean Valueb
6
1
1
4
1
a Ranked from most resistant to most sensitive based on Genus Mean 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 data are available so that the Final Acute Value is not unnecessarily
lowered.
b From Table la.
46
Draft November 12, 2004
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Table 2b. Ranked Saltwater Genus Mean Acute Values
Number of Acute
.anka
17
16
15
14
13
12
11
10
9
8
7
6
5
4
3
2
Genus Mean
Acute Value
(US/L)
17,350
14,649
>10,000
>10,000
9,725
7,400
4,600
4,400
3,497
3,036
1,900
1,500
1,331
1,200
1,040
599
Species
SALTWATER SPECIES
Selenite
Fourspine stickleback,
Apeltes quadracus
Winter flounder,
Pseudopleuronectes
americanus
Blue mussel,
Mytilus edulis
Pacific oyster,
Crassostrea gigas
Atlantic silverside,
Menidia menidia
Sheepshead minnow,
Cyprinodon variegatus
Blue crab,
Callinectes sapidus
Pinfish,
Lagodon rhomboides
Summer flounder,
Paralichthys dentatus
Striped bass,
Morone saxatilis
Surf clam,
Spisula solidissima
Mysid,
Americamysis bahia
Copepod,
Acartia clausi
Copepod,
Acartia tonsa
Brown shrimp,
Penaeus aztecus
Dungeness crab,
Cancer magister
Haddock,
Species Mean
Acute Value
(ua/LV3
17,350
14,649
>10,000
>10,000
9,725
7,400
4,600
4,400
3,497
3,036
1,900
1,500
2,110
839
1,200
1,040
599
Values used to
Calculate Species
Mean Valueb
1
2
1
2
1
1
1
1
1
5
1
1
1
1
1
1
1
Melanogrammus aeglefinus
47
Draft November 12, 2004
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Table 2b. Ranked Saltwater Genus Mean Acute Values
Rank8
1
Genus Mean
Acute Value
fug/Li
255
Species
Bay scallop,
Argopecten irradians
Species Mean
Acute Value
255
Number of Acute
Values used to
Calculate Species
Mean Valueb
1
9,790
Selenate
Striped bass,
Morone saxatilis
9,790
a Ranked from most resistant to most sensitive based on Genus Mean Acute Value. Inclusion of
"greaterthan" and "less than" values does not necessarily imply a true ranking, but does allow
use of all genera for which data are available so that the Final Acute Value is not unnecessarily
lowered.
b From Table Ib.
Selenite
Fresh Water
Final Acute Value = 5 14.9 ng/L
Criterion Maximum Concentration = (514 .9 ng/L) -=- 2 = 257 |ig/L
Salt Water
Final Acute Value = 2 53.4 ng/L
Criterion Maximum Concentration = (253 .4 ng/L) -=- 2 = 127 ng/L
Selenate
Fresh Water
Final Acute Value = 834.4 ng/L (calculated at a sulfate level of 100 mg/L from GMA Vs)
Criterion Maximum Concentration = (834.4 ng/L) -^ 2 = 417 ng/L ( at a sulfate level of 100 mg/L)
Pooled Slope = 0.5812 (see Appendix A)
In (Criterion Maximum Intercept) = ln(417.2) - [slope x ln(100)]
= 6.0335 - (0.5812 x 4.605) = 3.357
Criterion Maximum Concentration for Selenate (at a sulfate level of 100 mg/L) = 6
48
Draft November 12, 2004
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Table 3a. Ratios of Freshwater Species Mean Acute Values for Selenite and Selenate.
Selenite
Sensitivity
Rank from
Table 2aa
Species
Selenite
Species Mean
Acute Value
fus/L)b
Selenate
Species Mean
Acute Value at
Sulfate= 100
fue/Lt
Ratio
FRESHWATER SPECIES
28
27
26
25
24
23
22
21
20
19
18
17
16
15
14
Leech,
Nephelopsis obscura
Midge,
Tanytarsus dissimilis
Midge,
Chironomus decorus
Midge,
Chironomus plumosus
Common carp,
Cyprinus carpio
Snail,
Aplexa hypnorum
Bluegill,
Lepomis macrochirus
Goldfish,
Carassius auratus
Snail,
Physa sp.
White sucker,
Catostomus commersoni
Flannelmouth sucker
Catostom us latipinn is
Arctic grayling
Thymallus articus
Channel catfish,
Ictalurus punctatus
Colorado squawfish,
Ptychocheilus lucias
Mosquito fish,
Gam busia affin is
Yellow perch,
Perca flavescens
Golden shiner,
203,000
42,500
48,200
25,934
35,000
34,914
28,500
26,100
24,100
30,176
19,100
15,675
13,600
12,801
12,600
11,700
11,200
1,515,661
NAC
50,727
NA
NA
616,816
216,033
NA
NA
NA
27,380
94,159
226,320
18,484
NA
NA
NA
0.134
NA
0.95
NA
NA
0.057
0.132
NA
NA
NA
0.698
0.166
0.06
0.693
NA
NA
NA
Notoemigonus crysoleucas
49
Draft November 12, 2004
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Table 3a. Ratios of Freshwater Species Mean Acute Values for Selenite and Selenate (continued).
Selenite
Sensitivity
Rank from
Table 2aa
13
12
11
10
9
8
7
6
5
4
3
2
1
Species
Chinook salmon,
Oncorhynchus tshawytscha
Coho salmon,
Oncorhynchus kisutch
Rainbow trout,
Oncorhynchus mykiss
Brook trout
Salvelinu sfontinalis
Bonytail
Gilas elegans
Worm,
Tubifex tubifex
Razorback sucker,
Xyrauchen texanus
Flagfish,
Jordanellafloridae
Amphipod,
Gammarus pseudolimnaeus
Fathead minnow,
Pimephales promelas
Striped bass,
Morons saxatilis
Hydra,
Hydra sp.
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Ceriodaphnia affinis
Cladoceran,
Ceriodaphnia dubia
Amphipod,
Hyalella azteca
Selenite
Species Mean
Acute Value
( U2/L)b
15,596
7,240
10,488
10,200
9,708
7,710
7,679
6,500
3,489
2,209
1,783
1,700
905.3
1,987
<603.6
440
461.4
Selenate
Species Mean
Acute Value at
Sulfate= 100
( ue/L)b
83,353
29,141
43,192
NA
10,560
NA
10,309
NA
2,315
11,346
NA
25,032
3,314
3,420
NA
842
1,397
Ratio
0.187
0.248
0.243
NA
0.919
NA
0.745
NA
1.507
0.195
NA
0.068
0.273
0.581
NA
0.523
0.33
a Ranked from most resistant to most sensitive based on selenite Genus Mean Acute Value (from Table 2a).
b From Table la.
CNA = Not Available
50
Draft November 12, 2004
-------
Table 3b. Ratios of Saltwater Species Mean Acute Values for Selenite and Selenate.
Sensitivity
Rank from
Table 2ba
8
Species
Striped bass,
Morone saxatilis
Selenite
Species Mean
Acute Value
(>g/L)b
SALTWATER SPECIES
3,036
Selenate
Species Mean
Acute Value
(>g/L)b
9,790
Ratio
0.31
a Ranked from most resistant to most sensitive based on Genus Mean Acute Value (from Table 2b).
b From Table Ib.
51 Draft November 12, 2004
-------
«
I!
u
o
O
HI
104:
103
10
Ranked Summary of Selenite GMAVs
Freshwater
C rlt rH Main in Coic* itBttoi - 25? s [igrt. 9i K t Ife
0.2 0.4 O.i
% Rank GMAVs
o.E 1
D F Fernet Milt; rt brat
Figure 1. Ranked summary of selenite GMAVs (freshwater).
52
Draft November 12, 2004
-------
c
o
=a «S
Kf
"c
o>
E
o
o
+J
u
111
0>
-1-1
"c
"3>
10
Ranked Summary of Selenite GMAVs
Saltwater
DO
SalH.Ht r F lial rt;i t '...SHe - 2S3.3 pq.'L &i k l tt
Crlt r6 Uaxhiim Cui«iti3tt:.i - 126.7
0.2 0.4 O.G
% Rank GMAVs
0.8
Figure 1. Ranked summary of selenate GMAVs (saltwater).
53
Draft November 12, 2004
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Ranked Surnwy of Sdenate GMAV&
UJ
0) 1000 -d
IS
100
Fneshwater
0.0
0.2
- B3U IQ.I a feia aa its -
cm re Itexmm CoceiWa -
0.4
0.6
0.8 1.0
D Fra*«Be-huatetrate
Figure 3. Ranked summary of selenate GMAVs (freshwater) at a sulfate level of 100 mg/L.
54
Draft November 12, 2004
-------
Review and Analysis of Chronic Data
Since the issuance of the 1987 chronic criterion of 5 (ig/L, considerable information has come forth
regarding the route of exposure of selenium to aquatic organisms. Studies have shown that diet is the
primary route of exposure that controls chronic toxicity to fish, the group considered to be the most
sensitive to chronic selenium exposure (Coyle et al. 1993; Hamilton etal. 1990; Hermanutz et al. 1996).
Chronic tests in which test organisms were exposed to selenium only through water and which have
measured selenium in the tissue of the test species have produced questionably low chronic values based
on the tissue concentrations. Some ofthese water-only exposures have required aqueous concentrations
of selenium of greater than 300 (ig/L to attain body burdens sufficient to achieve a chronic response that
would have been reached in the real world at aqueous concentrations approximately 30 times lower
(Cleveland et al. 1993; Gissel-Nielsen and Gissel-Nielsen 1978).
Because diet controls selenium chronic toxicity in the environment and water-only exposures require
unrealistic aqueous concentrations in order to elicit a chronic response, only studies in which test
organisms were exposed to selenium in their diet alone or in their diet and water were considered in the
derivation of a chronic value. To be able to use the chronic study results, the measurements had to
include selenium in the test species tissue. Both laboratory and field studies were considered in the
review process. Chronic studies reviewed were obtained through a literature search extending back to
the last revision review, from information supplied to U.S. EPA through the Notice of Data Availability,
and using the references cited in previous selenium criteria documents.
Selection of Medium for Expressing Chronic Criterion
Whole-body tissue concentration of selenium on a dry weight basis, for species eliciting the chronic
response, was selected as the medium from which to base the chronic criterion value. As discussed
above, a water-based criterion is not appropriate for selenium because diet is the most important route of
exposure for chronic toxicity. The option of basing the chronic criterion on the concentration of
selenium in prey species (that is, in the diet of the target species), was considered inappropriate for two
reasons: 1) the concentration of selenium in the diet is an indirect measure of effects observed in the test
species and is dependent on feeding behavior of the target species, and 2) selection of what organism to
sample to assess attainment of a criterion based on diet is problematic in the implementation of such a
criterion. Sediment has also been proposed as a medium upon which to base the selenium chronic
criterion (Canton and Van Derveer 1997; Van Derveer and Canton 1997), but because of the patchiness
55 Draft November 12, 2004
-------
of selenium in sediment and an insufficient amount of data to support a causal link between
concentrations of selenium in sediment and chronic effects observed in fish (see Hamilton and Lemly
1999, for a review), a sediment-based criterion was rejected.
Besides being a direct link to chronic endpoints, a tissue-based criterion has the positive attributes of
integrating many site-specific factors, such as chemical speciation and rates of transformation, large
variations in temporal concentrations in water, types of organisms constituting the food chain, and rates
of exchange between water, sediment, and organisms (Hamilton, in preparation; U.S. EPA 1998).
Whole-body tissue was selected over specific tissue types, such as ovary, liver, kidney or muscle because
of practical reasons of sampling and because a sufficient data base containing chronic effects based on
whole-body tissue is present in the literature. Ovaries may be the best tissue to link selenium to
reproductive effects because of its role in the maternal transfer of selenium to eggs, and embryo-larval
development being one of the most sensitive endpoint for chronic effects. However, ovarian tissue is
also only available seasonally and sometimes difficult to extract in quantities sufficient for analysis,
especially in smaller fish species. Whole-body larval tissue is also not practical due to sampling and
seasonal constraints.
To increase the number of studies in which chronic effects could be compared with selenium
concentrations in whole-body tissue, the relationships between selenium concentrations in whole-body
and selenium concentrations in ovary, liver, and muscle tissues were estimated. Data from 4 dietary
exposure studies that sampled whole-body as well as muscles, ovary, or liver allowed the projection of
whole-body concentrations as a function of concentrations in these individual tissues. It was not possible
to estimate such relationship for kidneys and carcass because of insufficient data. One species (bluegill
sunfish) comprised over 90 percent of the data evaluated for these relationships.
Median concentrations of selenium in the whole-body were projected as a linear function of selenium
concentrations in ovaries and liver, or as an exponential function of the natural logarithm of selenium
concentrations in muscles (Figure 4; Appendix H). When selenium concentration in more than one organ
or tissue was available, muscle tissue was used preferentially for converting into an equivalent whole-
body value. Where appropriate, whole-body selenium concentrations were estimated from selenium
concentrations in muscle, ovary and liver according to the following equations (see Appendix H for
details on statistical analyses):
56 Draft November 12, 2004
-------
Muscle to Whole Body Conversion
m
"5
c.
c
CO
m HI 33 m
[Se] in muscle tissue (^g/g dw)
Ovary to Whole Body Conversion
"a
O
m
Q)
cn
y = 0.02 + 0.
zn c a:
[Se] in ovary tissue (prfg eta'1)
Liver to Whole Body Conversion
dl
3,
o
CD
y =-0.26 + 0.31 x
ZD 4d 6D 33
[Se] In liver tissue (pg/g
im
Figure 4. The quantile regression curves project median selenium concentrations in the whole body of
bluegill, largemouth bass, tilapia and carp as a function of selenium concentrations in their
tissues. Most data are from bluegill. Estimates of model parameters minimize the sum of
weighted absolute deviations (see Appendix H for details about statistical analyses).
57
Draft November 12, 2004
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[Sewhole.body] = exp(0. 133 1 + (0.8937 x ln[Semuscle])) (I)
[Sewhole.body] = 0.0173 + (0.4634 x [Seovary]) (II)
[Sewhole.body] = -0.2609 + (0.307 1 x [Se^]) (III)
Chronic studies that reported selenium concentrations in tissues based on wet weight were converted to
dry weight using a moisture content of 0.80 (U.S. EPA 1985b), unless specified otherwise. Note that
because conversion from wet to dry weight and from tissue to whole-body selenium concentration can
increase uncertainty in the estimate, site-data analysts should develop their own conversion factors
whenever possible to improve accuracy. The basis for such factors can be obtained from local historical
data or from newly acquired data specific for that site and species.
Calculation of Chronic Values
In aquatic toxicity tests, chronic values have usually been defined as the geometric mean of the highest
concentration of a toxic substance at which no adverse effect is observed (highest no observed adverse
effect concentration, NOAEC) and the lowest concentration of the toxic substance that causes an adverse
effect (lowest observed adverse effect concentration, LOAEC). The significance of observed effects is
determined by statistical tests comparing responses of organisms exposed to natural concentrations of the
toxic substance (control) against responses of organisms exposed to elevated concentrations. Analysis of
variance is the most common test employed for such comparisons. This approach however, has its
limitations. Since neither NOAEC or LOAEC are known in advance and the number of concentrations
that can be tested is constrained by logistic and financial resources, observed effects of elevated
concentrations may not permit accurate estimates of chronic values. For instance, if all elevated
concentrations had high adverse effects or if the difference in concentrations between two significantly
different treatments was large, it would not be possible to define either 1he NOAEC or LOAEC with
precision. Furthermore, as the concentration of some substances (e.g., selenium) naturally varies among
ecosystems, a concentration that is above the normal range at one site, maybe within the normal range at
a different location. In this approach to calculate chronic values, natural variation in concentrations of a
substance implies that controls are site specific, and thus multiple tests are needed to define the chronic
value at different locations.
58 Draft November 12, 2004
-------
An alternative approach to calculate chronic values focuses on the use of regression analysis to define the
dose-response relationship. With a regression equation, which defines the level of adverse effects as a
function of increasing concentrations of the toxic substance, it is possible to determine the concentration
that causes a relatively small effect, for example a 5 to 30 percent reduction in response. A reduction of
20 percent in the response observed at control (EC20) was used as 1he chronic value because it represents
a low level of effect that is generally significantly different from the control (U.S. EPA 1999). Smaller
reductions in growth, survival, or other endpoints only rarely can be detected statistically. Effect
concentrations associated with such small reductions have wide uncertainty bands, making them
unreliable for criteria derivation. Adverse effects are generally modeled as asigmoid function of
increasing concentrations of the toxic substance (Figure 5).
Dose-Response Relationship
C
o
Q.
(A
0)
a:
Seleniun Concentration
Figure 5. Reductions in survival, growth or other responses of organisms are often modeled as a sigmoid
function of increasing concentrations of selenium, or any other toxic substance.
A logistic regression was used to model negative effects of increasing concentrations of selenium on
growth, survival, or percent of normal individuals (without deformities) of several aquatic species. The
equations that described such functions were then used to estimate the concentration that promoted a 20
percent reduction in response observed at control levels (EC20). These analyses were performed using
the Toxic Effects Analysis Model software (version 0.02; R Erickson, U.S. EPA Duluth).
59
Draft November 12, 2004
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Only data sets that met the following conditions were included in the analysis: (1) the experiment had a
control treatment, which made it possible to define response levels at natural concentrations of selenium,
(2) and at least four concentrations of selenium. (3) The highest tested concentration of selenium caused
>50 percent reduction relative to the control treatment, and (4) at least one tested concentration of
selenium caused <20 percent reduction relative to the control treatment to ensure that the EC20 was
bracketed by tested concentrations of selenium. When the response was expressed as percentages (e.g.,
percent survival), transformed values (arcsin of the square root) were used to homogenize the variance.
Logistic regression assumes that a logistic model describes the log dose-response curve. For a visual
display of such model, a logistic curve with three parameters was fitted to each data set using nonlinear
least-squares regression analysis (Draper and Smith 1981). The logistic model was
where x symbolizes the selenium concentration in the organism's tissues, y is the response of interest
(survival, growth, or reproduction), and yg, a and b are model parameters estimated by the regression
analysis. The yg parameter represents the response of interest at background levels of selenium. The
graphs also include the 95 percent confidence interval for projections of the logistic model. These tasks
were performed in S-Plus version 6.0 (Insightful 2001).
When the data from an acceptable chronic test met the conditions for of the logistic regression analysis,
the EC20 was the preferred chronic value. When data did not meet the conditions, best scientific
judgment was used to determine the chronic value. In this case the chronic value is the geometric mean
of the NOAEC and LOAEC and termed the maximum allowable toxicant concentration (MATC). But
when no treatment concentration was an NOAEC, the chronic value is less than the lowest tested
concentration. And when no treatment concentration was a LOAEC, the chronic value is greater than the
highest tested concentration.
Evaluation of Freshwater Chronic Data for Each Species
Acceptable freshwater chronic toxicity data are currently available for an aquatic invertebrate
(Brachionus calyciflorous), eight different fish species, and a mix of fish species from the family
Centrarchidae in a total of 21 distinct studies (Table 4). Detailed summaries of each study are included
in Appendix I. Collectively, only these data were considered for the derivation of a final tissue residue
criterion for selenium. Below is a brief synopsis of the experimental design, test duration, relevant test
60 Draft November 12, 2004
-------
endpoints, and other critical information regarding the derivation of each specific chronic value. The
chronic toxicily values for other chronic selenium toxicity values and endpoints are included in
Appendix I.
Brachionus calyciflorus (freshwater rotifer)
This study reported by Dobbs et al. (1996) is one of two laboratory-based experiments (also see Bennett
et al. 1986) that involved exposing algae to selenium (in this case as sodium selenate) in water, and
subsequently feeding the algae to rotifers which were in turn fed to fish (fathead minnows). In this
particular study, the rotifers and fish were exposed to the same concentrations of sodium selenate in the
water as the algae, but received additional selenium from their diet (i.e., the algae fed to rotifers and the
rotifers fed to fish). The overall exposure lasted for 25 days. Rotifers did not grow well at
concentrations exceeding 108.1 (ig Se/L in water, and the population survived only 6 days at selenium
concentrations equal to or greater than 202.4 (ig Se/L in the water (40 (ig Se/g dw in the algae).
Regression analysis of untransformed growth data (dry weight) determined 4 day post-test initiation
resulted in a calculated EC20 of 42.36 (ig Se/g dw tissue (Table 4).
Oncorhynchus tshawytscha (chinook salmon)
Hamilton et al. (1990) conducted a 90-day growth and survival study with swim-up larvae fed one of two
different diets. The first diet consisted of Oregon moist pellets where over half of the salmon meal was
replaced with meal from selenium-laden mosquitofish (Gambusia affinis) collected from the San Luis
Drain, CA (SLD diet). The second diet was prepared by replacing half the salmon meal in the Oregon
moist pellets with meal from low-selenium mosquitofish (i.e., the same relatively uncontaminated
mosquitofish that were used in the control diet) and spiked with seleno-DL-methionine (SeMe diet).
Analysis of the trace element composition in the two different diets indicated that while selenium was the
most toxic element in the SLD diet, concentrations of boron, chromium, iron and strontium in the high-
selenium mosquitofish replacement diet (SLD diet type) were slightly elevated compared to the
replacement diet composed of uncontaminated control mosquitofish that were spiked with organic
selenium (SeMe diet type). These trace elements were, however, only 1.2 (e.g., iron) to 2.0 times (e.g.,
chromium) higher in the SLD diet than the SeMe diet, which contained the following measured
concentrations (dry weight basis) in the food: boron-10 (ig/g; chromium- 2.8 (ig/g, iron- 776 (ig/g, and
strontium-48.9 (ig/g.
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During the test, the survival of control chinook salmon larvae and larvae fed the lowest dietary selenium
concentrations in either dietary exposure type (SLD and SeMe, respectively, consuming food at
approximately 3 (ig Se/g dw) exceeded >97 percent up to 60 days post-test initiation. Between 60 and 90
days of exposure, however, the control survival declined significantly. Therefore, only data collected up
to 60 days post-test initiation was considered for analysis. Regression analysis of untransformed growth
data after 60 days of exposure resulted in a calculated EC20 of 15.74 (ig Se/g dw tissue for fish fed the
SLD diet type, and 10.47 (ig Se/g dw tissue for fish fed the SeMe diet type (Table 4). Note: The
mosquitofish from San Luis Drain were not tested for contaminants other than certain key elements
suspected to be present in these fish. The San Luis Drain receives irrigation drainage from the greater
San Joaquin Valley; and therefore, there is the possibility that the mosquitofish used in this study may
have contained elevated levels of pesticides. The use of the SLD diet results assumes that selenium, and
not these other possible contaminants, was the cause of any adverse chronic effects.
Oncorhynchus mykiss (rainbow trout)
Hilton and Hodson (1983) reared juvenile rainbow trout on either a high (25 percent) or low (11 percent)
available carbohydrate diet supplemented with sodium selenite for 16 weeks. Body weights, feed:gain
ratios, and total mortalities were followed throughout the exposure every 28 days. Tissues (livers and
kidneys) were extracted for selenium analysis after 16 weeks. Fish fed the diets (low carbohydrate and
high carbohydrate) with the highest selenium concentration (11.4 and 11.8 (ig Se/g dw food,
respectively) exhibited a 45 to 48 percent reduction in body weight (expressed as kg per 100 fish)
compared to control fish by the end of the exposure, which the authors attributed to food avoidance.
With only two dietary exposure concentrations and a control, these data were not amenable to regression
analysis. The MATC for growth of juvenile rainbow trout relative to the final concentrations of selenium
in liver tissue of trout reared on the high carbohydrate seleniferous dietary type is the geometric mean
(GM) of 21.0 ng Se/g dw (NOAEC) and 71.7 ng Se/gdw (LOAEC), or 38.80 ng Se/g dw. Using the
equation III to convert the selenium concentration in liver tissue to a concentration of selenium in the
whole-body, the MATC becomes 11.65 (ig Se/g dw (Table 4). The calculated MATC for the same group
of experimental fish exposed to selenium in the low carbohydrate diet becomes 13.08 (ig Se/g dw tissue,
which is the same MATC for trout exposed for an additional 4 weeks based on the occurrence of
nephrocalcinosis in kidneys (see Hicks et al. 1984; Appendix I).
Hilton et al. (1980) employed a similar test design as Hilton and Hodson (1983) in a later experiment to
examine the narrow window at which selenium changes from an essential nutrient to a toxicant affecting
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juvenile rainbow trout. The food consisted of a casein-torula yeast diet supplemented with selenium as
sodium selenite. The experiment lasted for 20 weeks. During this time, the trout were fed to satiation 3
to 4 times per day, 6 days per week, with one feeding on the seventh day. Organs (liver and kidney) and
carcasses were analyzed for selenium from fish sacrificed at 4 and 16 weeks. No gross histopathological
or physiological effects were detected in the fish, although trout raised on the highest dietary level of
selenium (13.06 (ig Se/g dw) had a significantly lower body weight (wet basis), a higher feed:gain ratio,
and higher number of mortalities (10.7; expressed as number per 10,000 fish days). The MATC for
growth and survival of juvenile rainbow trout relative to the final concentrations of selenium in liver
tissue is the GM of the NOAEC (40 jig Se/g dw tissue) and the LOAEC (100 ng Se/gdw tissue), or
63.25 (ig Se/g dw. Using equation IE to convert selenium concentrations in the liver to selenium
concentrations in the whole body, the MATC becomes 19.16 (ig/gdw (Table 4).
Eggs and milt were obtained from ripe rainbow trout collected from reference streams and streams
containing elevated selenium from an active coal mine in Alberta, Canada (Holm 2002; Holmet al.
2003). Eggs were fertilized and monitored in the laboratory until swim-up stage for percent fertilization,
deformities (craniofacial, finfold, and spinal malformations), edema, and mortality. Similar
investigations were conducted in 2000 and in 2001. The effort in 2001 added a stream with an
intermediate level of selenium contamination and another reference stream. The only other notable
difference between 2000 and 2001 was the temperature at which the embryos were incubated; 8°Cin
2000 and 5°C in 2001. The author stated 5°C more closely approximated actual incubation temperatures
for rainbow trout eggs. No differences were observed for percent fertilization or mortality between the
reference and contaminated sites in both the 2000 and 2001 investigations. The frequencies of
embryonic deformities and edema were significantly greater in the stream affected by coal mining than in
the reference stream in the 2000 study. The average frequencies of embryonic craniofacial, skeletal and
finfold deformities in the contaminated stream were 7.7, 13.8 and 3.2 percent, respectively; the average
frequency of edematous embryos was 30.8 percent. The effect level for selenium was determined to be
the average selenium concentration in rainbow trout muscle tissue, 1.50 (ig Se/g ww. Muscle ww was
converted to dw using 75.84 percent moisture derived for rainbow trout and equation 1 was used to
convert selenium muscle dwto selenium in whole body dw. The chronic value determined for
embryonic abnormalities in rainbow trout (2000 study) was 5.79 (ig Se/g adult whole body dw. A
comparison of the frequency of embryonic deformities or edema between selenium contaminated and
reference streams with the 2001 data indicated there were no significant differences. AnEC20 value,
however, was computed for the relationship between craniofacial deformities and the concentration of
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selenium in eggs, 10.4 (ig Se/g eggs ww. Quantile regression was used to convert selenium in egg ww to
muscle ww using the rainbow data reported by Holm et al. (2003). The remaining conversion to the
whole body dw value of 5.85 (ig Se/g was made using 75.84 percent moisture and equation 1. See
Appendix I for details on these studies.
Oncorhynchus clarki (cutthroat trout)
No significant effects of bioaccumulated selenium on mortalities and deformities in the eggs, larvae, and
fry from wild-caught cutthroat trout from a reference and exposed site (Fording River, British Columbia,
Canada) were observed by Kennedy et al. (2000). The observations were made on eggs reared in well
water from spawning age females collected from the two locations (N = 17 and 20, respectively) and
fertilized by one male collected at each site. The mean selenium content in muscle tissue from adult fish
was 2.4 (ig/g dw tissue for fish collected from the reference site, and 12.5 (ig/g dw tissue for fish
collected from the Fording River. Using Equation I to convert the selenium concentration in muscle
tissue to a selenium concentration in the whole-body, the chronic value for this study was estimated to be
>10.92 (ig/g dw parental fish tissue (see Table 4).
Hardy (2002) fed cutthroat trout experimental diets containing a range of selenomethionine (0-10 (ig/g
dw) for 124 weeks. No significant growth or survival effects were observed in the adult fish over the 124
weeks which reached a whole body concentration of 12.5 (ig/g dw selenium after 44 weeks. Embryo-
larval observations (percent hatch and percent deformed) were not related to whole body selenium
concentrations in the spawning females (9.37 (ig/g dw) fed the selenium-laden diet for 124 weeks. The
chronic value for this study was determined to be >9.37 (ig Se/g dw.
Salvelinus fontinalis (brook trout)
Spawning brook trout were collected from streams with elevated selenium contaminated by coal mining
activity and from reference streams in 2000 and again in 2001 (Holm 2002; Holm et al. 2003) . Similar
to that described for rainbow trout above, fertilized eggs were monitored in the laboratory for percent
fertilization, deformities (craniofacial, finfold, and spinal malformations), edema, and mortality. The
only abnormality observed in the embryos spawned from the brook trout collected in 2000 at the
contaminated stream that had a frequency greater than the reference stream was cianiofacial deformity
(13.6 percent for the contaminated stream compared to 3.0 percent in the reference stream). The effect
level for craniofacial deformity in brook trout for the 2000 data was determined to be the average
selenium concentration in adult muscle tissue, 3.79 (ig Se/g wwor 13.2 (ig Se/g whole body dw using
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conversion factors (75.84percent moisture and equation 1). The only significant difference observed in
2001 brook trout was a greater frequency of finfold deformities in brook trout collected from Gregg
Creek (intermediate selenium levels) relative to the reference stream (4.1 percent in Gregg Creek
compared to 0.1 percent in the reference stream). The effect level for fmfold deformites in the 2001
study was estimated to be the concentration of selenium in brook trout eggs from Gregg Creek, 6.88 (ig
Se/g ww. Using the same conversion factors used for rainbow trout in the Holm study described above,
the chronic value in adult whole body dw is 12.4 (ig Se/g. See Appendix I for more details.
Salmonidae summary
Four of the studies with salmonids discussed above evaluated the effects of selenium directly on growth
of juvenile fish (Hamilton et al. 1990; Hilton and Hodson 1983; Hilton et al. 1980; Hicks et al. 1984),
while three of the studies evaluated the effects of selenium on embryo/larval survival and deformity
where exposure was through the parents (Hardy et al. 2002; Holm 2000; Holm et al. 2003; Kennedy et al.
2000). Of the studies based on embryo/larval survival and deformity where exposure was through the
parents, fry from hatchery brood fish were fed a selenium-spiked diet, grown to sexual maturity, and
spawned for the effects determination in the Hardy et al. study, and wild-caught adults from selenium
contaminated streams were spawned for the effects determination in the Holm studies and in the
Kennedy et al. study. Significant effects due to selenium exposure in these field exposed studies were
not observed for cutthroat trout (Hardy et al. 2002; Kennedy et al. 2000). Significant effects were
observed for rainbow trout and brook trout, albeit relatively minor effects in the latter species (Holm
2002; Holm et al. 2003). Although significant effects were not observed in the Hardy et al. and Kennedy
et al. studies, the data are meaningful with respect to the effect levels obtained for embryo-larval
development in Oncorhynchus, and thus retained for GMCV (10.66 (ig Se/g dw) calculation (Table 4).
Pimephales promelas (fathead minnows)
Chronic values for fathead minnows were derived from three laboratory-based studies and one mesocosm
study (Table 4). Two of the laboratory studies (Bennett et al. 1986 and Dobbs et al. 1996) involved
exposing algae to selenium (either as sodium selenite or sodium selenate) in water, and subsequently
feeding the algae to rotifers which were in turn fed to fathead minnows. In the Bennett et al. (1986)
study, larval fathead minnows were fed control (cultured in chambers without selenium containing algae)
or selenium-contaminated rotifers (cultured in chambers with selenium containing algae previously
exposed to sodium selenite in the water) in three separate experiments lasting 9 to 30 days. The different
experiments were distinguished by: 1) the day selenium-laden rotifers were first fed, 2) the day selenium-
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laden rotifers were last fed, and 3) the age of larvae at experiment termination. The results from the three
experiments reported by Bennett et al. (1986) were conflicting. Larval growth was significantly reduced
at whole-body selenium concentrations ranging from 43.0 to 51.7 (ig/g dw tissue in the first two
experiments (see Appendix I for conditions), but growth was not significantly reduced in larvae that had
accumulated 61.1 (ig/g dw tissue in the third experiment (Table 4). The geometric mean of these three
values, 51.40 (ig/g dw, was considered the chronic value for selenium for this test.
A similar test system was used by Dobbs et al. (1996), in which larval fathead minnows were exposed to
the same concentrations of sodium selenate in the water as their prey (rotifers), but also received
additional selenium from the consumption of the selenium-contaminated rotifers. In this study, the
fathead minnows did not grow well at concentrations exceeding 108.1 (ig Se/L in water, and they
survived only to 11 days at selenium concentrations equal to or greater than 393.0 (ig/L in the water (75
(ig Se/g dwin the diet, i.e., rotifers). The LOAEC for retarded growth (larval fish dry weight) in this
study was <73 (ig Se/g dw tissue (Table 4).
In contrast to the above laboratory-based food chain studies, Ogle and Knight (1989) examined the
chronic effects of only elevated foodborne selenium on growth and reproduction of fathead minnows.
Juvenile fathead minnows were fed a purified diet mix spiked with inorganic and organic selenium in the
following percentages: 25 percent selenate, 50 percent selenite, and 25 percent seleno-L-methionine.
The pre-spawning exposure lasted 105 days using progeny of adult fathead minnows originally obtained
from the Columbia National Fishery Research Laboratory, and those obtained from a commercial fish
supplier. After the 105 day exposure period, a single male and female pair from each of the respective
treatment replicates were isolated and inspected for spawning activity for 30 days following the first
spawning event of that pair. There was no effect from selenium on any of the reproductive parameters
measured, including larval survival, at the dietary concentrations tested (5.2 to 29.5 (ig Se/g dw food).
Sub-samples of larvae from each brood were maintained for 14 days post-hatch and exhibited >87.4
percent survival. The pre-spawning adult fish fed a mean dietary level of 20.3 pg Se/g dw did exhibit a
significant reduction in growth compared to controls (16 percent reduction), whereas no effect on growth
occurred in the fish fed 15.2 (ig Se/g dw. The whole-body chronic value, as determined by the GM of the
NOAEC and 1he LOAEC measured at 98 days post-test initiation, was 5.961 (ig/g dw tissue (Table 4).
The chronic value of 5.961 (ig/g dw determined for growth after 98 days of exposure to pre-spawning
fathead minnow adults (Ogle and Knight, 1989) was approximately an order of magnitude lower than the
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growth effects to fathead minnow observed in Bennettet al. (1986) and Dobbs et al (1996). The length
of exposure in the Ogle and Knight test was more than twice as long as either Bennett et al. or Dobbs et
al., suggesting a longer duration was needed in order to detect any growth effects from selenium.
However, in addition to the absence of effects observed for the reproductive parameters measured,
survival of larvae hatched from parents exposed to each of the five selenium treatments (including those
in which growth was affected) was not affected.
Other studies (Bryson et al. 1984; Bryson et al. 1985a; Coyle et al. 1993; Hermanutz et al. 1996) have
found larval deformities and larval survival to be the most sensitive endpoint to fish. This also appears
true for fathead minnows. Schultzand Hermanutz (1990) examined the effects of selenium in fathead
minnow larvae transferred from parental fish (females). The parental fathead minnows were originally
exposed to selenite which was added to artificial streams in a mesocosm study. The selenite entered the
food web which contributed to exposure from the diet. Spawning platforms were submerged into treated
and control streams. The embryo samples that were collected from the streams were brought into the
laboratory and reared in incubation cups which received stream water dosed with sodium selenite via a
proportional diluter. Edema and lordosis were observed in approximately 25 percent of the larvae
spawned and reared in natural water containing 10 (ig Se/L. Selenium residues in the ovaries of females
from the treated stream averaged 39.27 (ig/g dw. Using equation II to convert the selenium concentration
in the ovaries to a concentration of selenium in the whole-body, the chronic value for this species was
estimated to be <18.21 (ig Se/g dw (Table 4).
Since Ogle and Knight reported that food in the higher selenium concentrations remained uneaten and
fish were observed to reject 1he food containing the higher selenium concentrations, the authors
suggested that the decreased growth was caused by a reduced palatability of the seleniferous food items.
This is a common observation also noted by Hilton and Hodson (1983) and Hilton et al. (1980) and
apparent in Coughlan and Velte (1989). Given the no observed effect to larval survival and the apparent
non-toxicological effect on growth in the Ogle and Knight study, the SMCV for fathead minnows does
not include the 5.961 (ig/g dw chronic value.
Also excluded from the SMCV calculation for fathead minnows were the chronic value and LOAEC
estimated from the laboratory food-chain experiments of Bennett et al. (1986) and Dobbs et al. (1996).
In both of these studies, the effect concentrations based on larval growth appear to be less sensitive than
the effect on larval edema and deformity observed in Schultz and Hermanutz (1990). The greater
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sensitivity of larval fathead minnows to selenium as measured by edema and deformity (lordosis) in the
Schultz and Hermanutz (1990) study is consistent with other studies using bluegill (Table 4); and thus,
the SMCV for falhead minnows of < 18.21 (ig/g dw was based on this endpoint.
Catostomus latipinnis (flannelmouth sucker)
Beyers and Sodergren (200 la) exposed flannelmouth sucker larvae to a range of aqueous selenate
concentrations (<1, 25.4, 50.6, 98.9, and 190.6 (ig/L) and respectively fedlhem a range of selenium in
their diet (rotifers containing <0.702, 1.35,2.02, 4.63, and 8.24 (ig/gdw). There were no survival or
growth effects observed after the 28 day exposure. The chronic value based on the concentration of
selenium measured in the larvae exposed to the highest test concentration was >10.2 (ig Se/g dw.
Xyrauchen texanus (razorback sucker)
Two laboratory exposure studies have been done with the endangered razorback sucker. In the first
study, Beyers and Sodergren (200la) exposed larval razorback suckers to the same aqueous and diet
concentrations as described above for the flannelmouth sucker. Similar to the results found for the
flannelmouth sucker, survival and growth of the razorback sucker larvae were not reduced afterthe 28
day exposure. The chronic value for this study based on selenium measured in the larvae at the end of
the test is > 12.9 (ig Se/g dw. In a second study, Beyers and Sodergren (200Ib) exposed larval razorback
suckers to a control water and three different site waters containing varying concentrations of selenium.
Two treatments were tested within each water type, fish fed rotifers cultured in the same water type (site
diet) and fish fed rotifers cultured in control water. There were no reductions in survival or growth in
fish exposed to both the site water and site diet compared to fish exposed to control water and control
diet. There were, however, reductions in growth in fish exposed to site water/site food compared to the
same site water and control food. The authors did not attribute the effect on larval growth by the diet to
selenium and cited several lines of evidence, including: (1) there was not a dose-response relationship in
the concentration of selenium in the food (rotifers) and growth, nor in 1he concentration of selenium in
the fish larvae and growth across the three water types; and (2) the site water type, identified as De
Beque, showed a significant reduction in the growth offish exposed to site water/site food relative to site
water/control food, but contained levels of selenium in the water (< l^g/L) and food (2.10 (ig/g dw)
typically lower than those that have been found to elicit effects. The chronic value for this study is > 42
(ig Se/g dw based on the whole body concentration of selenium in the larval razorback suckers exposed
to North Pond site water.
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Lepomis macrochirus (bluegill sunfish)
Applicable chronic data for bluegill sunfish can be grouped according to field exposure versus laboratory
exposure. In some field studies, chronic tolerance to selenium appears to be much higher than in
laboratory studies (Bryson et al. 1985a). In the Bryson et al. (1984, 1985a) and Gillespie and Baumann
(1986) studies, the progeny of females collected from a selenium contaminated reservoir, Hyco
Reservoir, Person County, NC and artificially crossed did not survive to swim-up stage, irrespective of
the origin of milt used for fertilization. Measured waterborne selenium concentrations prior to the
experiments ranged from 35 to 80 (ig/L. The whole-body tissue selenium concentration in the female
parent associated with this high occurrence of mortality of hatched larvae was <43.70 (ig/g dw tissue, as
reported by Bryson et al. (1985a), and <21.47 (ig/g dw tissue, as reported by Gillespie and Baumann
(1986) (Table 4). In the case of the latter, nearly all swim-up larvae from the Hyco Reservoir females
were edematous, none of which survived to swim-up. These chronic effect tissue values are in line with
the EC20 calculated for the occurrence of deformities among juvenile and adult fishes from the family
Centrarchidae collected from Belews Late, NC, i.e., 44.57 (ig Se/g dw (see Lemly 1993b, Table 4).
Bryson et al. (1985b) conducted juvenile survival toxicity tests using hatchery bluegill and various forms
of selenium spiked to an artificial diet as well as a diet consisting of zooplankton collected from Hyco
Reservoir. There was no effect on length or weight of the juvenile bluegill after 60 days of exposure.
The highest concentration of selenium measured in whole body fish tissues in these tests was in the
seleno-DL-cysteine-2X treatment (3.74 (ig Se/g dw). Bryson et al. (1985b) also examined percent hatch
and percent swim-up larvae from spawns using fish collected from Hyco Reservoir and a control site.
There were no differences in the Hyco measurements relative to the control. The concentration of
selenium in the liver of the parental Hyco bluegill was 18.6 (ig/gdw or 5.45 (ig Se/g dw whole body
using equation III for conversion. The chronic values for the juvenile bluegill test and the embryo-larval
development tests were >3.74 and >5.45 (ig Se/g dw whole body, respectively.
In contrast, the chronic effects threshold for larval survival in a combination laboratory waterborne and
dietary selenium exposure (Coyle et al. 1993), or even a long-term mesocosm exposure (Hermanutz et al.
1996), occurs at concentrations approximately 3 times lower than those recorded above (Table 4). In the
Coyle et al. (1993) study, two-year old pond reared bluegill sunfish were exposed in the laboratory to a
nominal 10 (ig Se/L in water (measured concentrations in respective dietary treatments ranging from 8.4
to 11 (ig/L) and fed (twice daily ad libitum) Oregon moist pellets containing increasing concentrations of
seleno-L-methionine. The fish were grown under these test conditions for 140 days. Spawning
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frequency, fecundity, and percentage hatch were monitored after 60 days when spawning began to occur.
There was no effect of the combination of the highest dietary selenium concentration (33.3 (ig Se/g dw)
in conjunction with waterborne selenium concentrations averaging 11 (ig/L on adult growth, condition
factor, gonadal somatic index, or the various reproductive endpoints (Appendix I). The survival of newly
hatched larvae, however, was markedly reduced; only about 7 percent survived to 5 days post-hatch.
Regression analysis on arcsin square root transformed fry survival data 5 days post-hatch resulted in a
calculated EC20 of 8.954 jig Se/g dw tissue (Table 4).
Hermanutz et al. (1996), as corrected by Tao et al. (1999), and peer reviewed in Versar (2000), exposed
bluegill sunfishto sodium selenite spiked into artificial streams (nominal test concentrations: 0, 2.5, 10,
and 30 (ig Se/L) which entered the food web, thus providing a simulated field-type exposure (waterborne
and dietary selenium exposure). A series of three studies were conducted over a 3 year period lasting
anywhere from 8 to 11 months. All three studies began exposure to adult bluegill sunfish in the fall and
ended the respective study in the summer of the following year. Winter temperatures averaged 4.1 and
4.5°C and spawning months (June-July) averaged 23.9 and 22.4°C, respectively for Studies II and III.
The Hermanulz et al. (1996) report contains the data presented in the Hermanutz et al. (1992) article
(Study I, 10 and 30 (ig/L exposures) as well as Studies Hand III (2.5 and 10 (ig/L and recovering
mesocosms). Spawning activity was monitored in the stream, and embryo and larval observations were
made in situ and from fertilized eggs taken from the streams and incubated in egg cups in the laboratory.
None of the adult bluegill exposed to the highest concentration of selenium in the water (Study I, mean
measured concentration equal to 29.4 (ig/L) survived. Incidence of edema, hemorrhage, and lordosis in
the larvae incubated in egg cups and spawned from fish exposed to 10 (ig Se/L were 100, 45 and 15
percent, respectively (see Hermanutz 1996 in Appendix I). Such health problems were not observed in
larvae from fish that were not exposed to elevated concentrations of selenium (control treatment). Rates
of edema, hemorrhage, and lordosis occurrence in larvae (egg cup data) from fish exposed to 2.5 (ig Se/L
were 0, 3.6 and 0 percent, respectively. Mean concentrations of selenium in fish tissues (whole body) of
the control, 2.5 and 10 (ig Se/L treatments were 1.95, 5.55, and26.46 (ig Se/g dw, respectively. Except
for the 2.5 (ig Se/L treatment, each value is a geometric mean of 2 replicates.
Results of this experiment were not suitable for regression analysis. Exposure of adult fish to 10 (ig Se/L
caused a small reduction in larval survival (in their first three days), from 75 to 57 percent. However,
responses lower than half of the values observed in control treatments are needed to adequately
characterize the slope of decline in survival (or growth, reproduction...) with increasing concentrations of
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selenium, ft is not sufficient to have only extremely low and high responses. Intermediate effects are
necessary to properly estimate the shape of the dose-response curve. The percent of larvae with edema
increased from 0 percent at the control and 2.5 (ig Se/L treatments to 100 percent in streams that received
10 (ig Se/L. With these data, it is not possible to accurately estimate the lowest concentration with
adverse effects (LOAEC) nor the rate at which incidence of edema increases with higher tissue
concentrations of selenium.
The chronic value for this study was estimated from results of analysis of variance (ANOVA) reported by
Tao et al. (1999). ANOVA was utilized to evaluate effects of elevated concentrations of selenium on
percent hatch, percent survival, maximum percent edema, lordosis, and hemorrhage, and minimum
percent healthy (egg cup data). Treatment effects were only significant for maximum percent edema and
minimum percent healthy (see their Table 4-19), and in no instance were differences between the 2.5 (ig
Se/L and control treatments significant (Dunnett's Means test, all probabilities > 0.1, see their Table 4-
20). These results clearly suggest that 1he 2.5 (ig Se/L treatment had no adverse impact onbluegill
larvae. They are further supported by analysis of the field nest data (see Hermanutz 1996 in Appendix I).
In this experiment, treatment had a significant effect on maximum percent edema (raw data and ranks)
and maximum percent hemorrhage (ranks only). Probabilities of differences between the 2.5 (ig Se/L and
control treatments were >0.2 for all response variables except maximum percent hemorrhage, which had
an estimated probability of 0.05 (raw data, P=0.022 for ranks; Dunnett's means test). Such values,
though, were well above the adjusted experiment-wise error rate for multiple comparisons (a'=0.0085,
a'=l-(l-a)1/t; a=0.05, k=6 comparisons; Sokal and Rohlf 1981), which takes into account the fact that
selenium effects were tested on six different response variables. Therefore, the chronic value for this
study, 12.12 (ig Se/g dry weight, was calculated as the geometric mean of tissue concentrations of
selenium in the 2.5 (NOAEC) and 10 (ig Se/L (LOAEC) treatments (5.55 and 26.46 (ig/g dw,
respectively).
The importance of diet in the bioaccumulation of selenium was demonstrated in one additional
experiment. Study in consisted of the addition of new adult bluegill to the same streams that received
the 2.5, 10 and 30 (ig/L sodium selenite during previous studies, but with all dosing of selenite halted.
The adult bluegills exposed only to dietary selenium present in the food web accumulated selenium to
levels very near to the levels accumulated during Study II in which aqueous selenium was also present
demonstrating the importance of diet on selenium accumulation. There were no effects (no effect on
larval survival, 0 percent deformities, 0 percent hemorrhaging), on the bluegill progeny in Study III even
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from fish that accumulated 11.7 and 14.5 (ig/g dw in the recovering 10 (ig/L streams, and 17.35 (ig/g dw
in the recovering 30 (ig/L stream. The lack of any effect on the Study III larvae suggests that although
dietary exposure would have been the predominant exposure route in both Study II and Study III,
environmental differences influenced the toxicological significance of the tissue concentrations.
A 90-day diet-only laboratory exposure in which juvenile bluegjll sunfish were fed a range of
selenomethionine concentrations added to Oregon moist did not have any significant effects on survival
(Cleveland et al. 1993). The authors did report a significant decrease in the condition factor (K) at the
diet treatment where bluegill whole body tissue concentrations were measured at 7.7 (ig Se/g dw. The
condition factor (weight x 105/length3) is reflective of the weight of the fish, and as discussed earlier, the
avoidance of food at similar dietary concentrations in other fish studies (Ogle and Knight 1989; Hilton
and Hodson 1983; Hilton et al. 1989; Coughlan and Velte 198 9) suggests the reduction in K is possibly a
non-toxicological effect. Given the very slight reduction in K (1.3 to 1.2) and the uncertain relevance of
growth data, the chronic value for this study was estimated at > 13.4 (ig Se/g dw.
Data from Lemly (1993a) indicate that over-wintering fish may be more susceptible to the effects of
waterborne and dietary selenium due to increased sensitivity at low temperature. The authors exposed
juvenile bluegill sunfish in the laboratory to waterborne (1:1 selenite:selenate; nominal 5 (ig Se/L) and
foodborne (seleno-L-methionine in TetraMin; nominal 5 (ig Se/gdw food) selenium for 180 days. Tests
with a control and treated fish were run at 4°C and 20°C with biological and selenium measurements
made every 60 days. Survival and whole-body lipid content were unaffected at 20°C (whole-body
selenium concentrations equal to 6 (ig/g dw) when compared to control fish. Fish exposed to the
combination low-level waterborne and dietary selenium at 4°C exhibited significantly elevated mortality
(40.4 percent) relative to controls (2.9 percent), and exhibited significantly greater oxygen consumption
and reduced lipid content, which are all indicative of an additional stress load. The chronic value for
juvenile bluegill sunfish exposed to waterborne and dietary selenium at 4°C was <7.9 (ig/g dw tissue,
whereas the chronic value for juvenile bluegill sunfish exposed to waterborne and dietary selenium based
on survival at 20°C was >6 (ig/g dw whole-body tissue.
Five of the studies discussed above evaluated the effects of selenium on fish larvae to which exposure
was through the parents. Three of these studies collected adult fish from Hyco Reservoir to which the
bluegill population had been exposed to elevated selenium concentrations for multiple generations
(Bryson et al. 1984; Bryson etal. 1985a; Gillespie and Baumann 1986), whereas the other two studies
72 Draft November 12, 2004
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exposed bluegill parents obtained from anuncontaminated source (Coyle et al. 1993; Hermanutz et al.
1996). The average of the chronic values reported for the Hyco studies was four times greater than the
value in the latter two studies. This difference may simply be the inability of the field tests to detect a
lower effect concentration than that which was observed at the site. However, Bryson et al. (1985a)
found no effects to larval survival from Hyco Reservoir females collected in an "unaffected area"
containing 19.18 (ig Se/gdw suggesting the possibility of tolerance through physiological or genetic
adaptation of the previous exposed bluegill population at Hyco Reservoir.
Acquisition of tolerance to selenium has also been implied in the literature for other fish species. For
example, Kennedy et al. (2000) suggested tolerance at the cellular level as an explanation for the normal
development of early life stages for cutthroat trout collected from a stream containing 13.3 to 14.5 (ig
Se/L in the water column. These authors reported that the overall frequency of larval deformities in the
exposed population was less than 1 percent, and in one fish containing eggs with 81.3 (ig Se/gdw, there
were 0.04 percent pre-ponding deformities and 3.3 percent larval mortalities. It should be noted that the
acquisition of tolerance to selenium has been hypothesized (Kennedy et al. 2000), but has not yet been
substantiated. Other than the Kennedy et al. study, tolerance to selenium in one of the endpoints
consistently sensitive to fish (embryo-larval development) has not been reported in the literature and its
reality is uncertain at this time. However, given the need to protect sensitive populations of species, the
chronic values for the studies in which eggs and larvae were obtained from bluegill adults that were
exposed to elevated selenium for multiple generations (i.e., Bryson et al. 1984; Bryson et al. 1985a;
Gillespie and Baumann, 1986) were not included in the SMCV calculation.
Morone saxitilis (Striped bass)
The only remaining applicable chronic value for selenium was determined from a laboratory dietary
exposure conducted using yearling striped bass (Coughlan and Velte 1989). During the experiment, the
bass were fed contaminated red shiners (38.6 (ig Se/g dw tissue) fromBelews Lake, NC (treated fish) or
golden shiners with low levels of selenium (1.3 (ig/g dw tissue) purchased from a commercial supplier
(control fish). The test was conducted in soft well water and lasted up to 80 days. During the
experiment, all fish were fed to satiation 3 times per day. Control fish grew well and behaved normally.
Treated fish behaved lethargically, grew poorly due to a significant reduction in appetite, and showed
histological damage, all eventually leading to the death of the animal. The final selenium concentration
in muscle of treated striped bass averaged from 17.50 to 20.00 (ig/g dw tissue (assuming 80 percent
moisture content), which was 3.2 to 3.6 times higher than the final selenium concentrations in control
73 Draft November 12, 2004
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striped bass, which averaged 5.500 (ig/g dw tissue. Using equation I to convert the selenium
concentration in muscle tissue to a selenium concentration in the whole-body, the chronic value for this
species was determined to be <14.75 (ig/g dw (Table 4).
Formulation of the Final Chronic Value (FCV) for Selenium
The lowest GMCV in Table 4 is for bluegill, 9.500 (ig/g dw whole body, which is the geometric mean of
chronic values from the laboratory study of Coyle et al. (1993), the laboratory study of Lemly (1993a)
and the macrocosm exposure study of Hermanutz et al. (1996). Several of 1he chronic values listed in
Table 4 were not used in the calculation of this GMCV. These values fall under several categories. The
"less than" values tabulated for Bryson et al. (1984) and Gillespie and Baumann (1986) for Hyco
Reservoir bluegill were not used to because they only indicate a chronic value in a range that includes
9.500 (ig/g dw. The "greater than" values for Bryson et al (1985b) were not used because similar studies
with bluegill sunfish provided more meaningful information on effect levels. The "greater than" value
for the recovering systems in Study III from Hermanutz et al. (1996) was not used in the mean calculation
because, as previously discussed in the Lepomis section, less tolerance was observed in 1he freshly
exposed systems of Study II. The Table 4 results for Bryson et al. (1985a) and Lemly (1993b) were also
not used in calculating the bluegill GMCV. Bryson et al. (1985a) indicated a chronic value for Hyco
Reservoir bluegill somewhere between 20.29 and 43.70 (ig/g dw. Lemly (1993b), appearing in Table 4
under the category Centrarchidae, the family to which bluegill belong, yielded a chronic EC20 of 44.57
(ig/g dw specific for fish from Belews Lake, NC, again substantially above the GMCV of 9.500 (ig/g dw.
It is not known whether historical exposure to elevated selenium concentrations, such as occurred at
Belews Lake and Hyco Reservoir, will dependably lead to this magnitude of increase in the chronic
tolerance of resident fish.
The Lemly (1993a) laboratory results, indicating achronic value for over-wintering juvenile bluegill
sunfish of <7.91 (ig/g dw, are not completely comparable to the other values used to calculate the bluegill
GMCV. This study involved an additional natural stress, exposure to a simulated winter low temperature
of 4°C. In this study, juvenile bluegill sunfish exposed to the over-wintering temperature 4°C appeared
to accumulate more selenium in whole-body tissues (7-8 (ig Se/g dw tissue) relative to those exposed at
20°C (5-6 (ig Se/g dw tissue), but also exhibited increased signs of chronic toxicity. Because this stress
occurs annually to one degree or another in nearly all the country, the FCV was lowered to 7.91 (ig/g dw
to protect sensitive fish species Although the literature contains little information on the temperature-
dependence of selenium toxicity, Lemly's study (further summarized in Appendix I) was judged to be
74 Draft November 12, 2004
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sufficiently definitive to merit lowering the FCV. The study showed a clear effect on juvenile bluegill
survivorship when tissue concentrations reach 7.91 (ig Se/g dw under extended cold temperature
conditions.
In the Lemly (1993a) study, the aulhor relates the selenium induced hematological changes to gill
lamellar damage (possible reasons cited were the collection of cell parts in capillaries restricting blood
flow increasing pressure and rupturing or swelling lamellar vessels, and smaller red cells becoming
tightly packed in vessels). The author postulates that an imbalance between respiratory demands (i.e.,
Se-exposed fish used more O2 at both 4°C and 20°C) and decreased respiratory capacity could have
constituted a stress that resulted in reduced body condition and lipid content offish in the cold treatment.
The condition of the combination of selenium-induced elevation in energy demand and reductions in
feeding due to cold temperature and short photoperiod, leading to severe depletion of stored body lipid
was termed, Winter Stress Syndrome.
The Guidelines indicate that the chronic criterion (in this case the FCV) is intended to be a good estimate
of the threshold for unacceptable effect. The Guidelines point out that the threshold for unacceptable
effect does not equate with a threshold for any adverse effect. For example, some adverse effects,
possibly even a small reduction in survival, growth, or reproduction may occur at this threshold. If over-
wintering bluegill are as sensitive as indicated by the Lemly (1993a) results, some reduction in survival
(compared to populations accumulating lesser concentrations of selenium or exposed to less severe
winter temperatures) would occur at the FCV. Nevertheless, other studies, those of Lemly (1993b) and
Bryson et al. (1985a), suggest that historically exposed populations may not be as sensitive as the
organisms studied by Lemly (1993a).
The bluegill exposed to selenium at 4°C in the Lemly (1993a) study accumulated 7.91 (ig/g dw, whereas
those exposed to Se at 20°C accumulated only 5.74 (ig/g dw. The increase in the concentration of
selenium in whole body tissue at4°C was apparently due to reductions in lipid and body weight caused
by decreased feeding by the j uvenile bluegill resulting in a concentration of selenium in their tissues. If
this concentration of selenium in tissues occurs in sensitive overwintering fish in nature, a criterion of
5.85 (ig/g dw (the selenium tissue concentration in the 4°C exposure after 60 days) in for fish collected
during the summer or fall months might be warranted to protect the selenium-sensitive fish during the
winter months. However, it is not understood at this time whether fish in nature do concentrate selenium
during the winter. The Lemly (1993a) study used an artificial diet spiked with seleno-methionine.
75 Draft November 12, 2004
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Although the 20°C fish did not show signs of food avoidance to the Se-spiked food, as discussed earlier
in this section, other studies did observe decreased feeding and effects on growth.
If sensitive juvenile fish are indeed adversely affected during winter months, field studies should indicate
an altered age structure relative to selenium whole body tissue levels. May et al. (2001) reported that an
analysis of the size structure of bluegill populations in the Republican River and in 7 reservoirs within
this river's basin, where mean tissue concentrations ranged from 2.85 to 8.84 |o,g Se/g dw, revealed large
numbers of small fishes. Similar patterns in the size structure offish populations were observed for 7
additional species: common carp, green sunfish, channel catfish, largemouth bass, gizzard shad, black
bullhead, and river carpsucker.
Given the uncertainty of juvenile fish concentrating selenium over the winter, anFCV of 7.91 (jg Se/g
dw is recommended. However, if the concentration of selenium in whole body fish tissues approaches
5.85 (ig Se/g dw during the summer or fall months, it is recommended fish be sampled during the winter
to determine if they exceed the FCV of 7.91 (ig Se/g dw.
The FCV may not necessarily protect fish in a hypothetical environment where tiey are exposed only via
water and not via diet. If the organisms are provided with an uncontaminated diet, then exceedingly high
water concentrations, possibly above the acute criterion, are needed to elicit effects, but such effects may
occur at tissue concentrations below the FCV (Cleveland et al. 1993; Gissel-Nielsen and Gissel-Nielsen
1978). This is not a practical limitation, however, since water-only exposure of selenium is not
representative of the actual exposure of selenium to aquatic organisms in the environment.
The FCV of 7.91 (ig/g dw was based on a scientific interpretation of the data presented in Table 4.
Although the FCV is derived from a limited number of species (9 species/7 genera), it is intended to be
protective of aquatic organisms across the United States. There may be aquatic communities whose fish
assemblage may contain species with different sensitivities to selenium compared to those listed in
Table 4. Furthermore, even within the Table 4 bluegill data, there is a range of reported tissue NOAECs
from various sites. Consequently, results from appropriate site-specific studies could be used to modify
the criterion.
76 Draft November 12, 2004
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A comparison of the FCV to tissue values measured in U.S. Fish and Wildlife Service's National
Contaminant Biomonitoring Program and U.S. Geological Survey's National Water Quality Assessment
(NAWQ A) program is provided in Appendix!.
77 Draft November 12, 2004
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Table 4. Freshwater Chronic Values from Acceptable Tests
Species
Brachionus
calyciflorus
rotifer
Oncorhynchus
tshawytscha
chinook salmon
Oncorhynchus
tshawytscha
chinook salmon
Oncorhynchus
mykiss
rainbow trout
Oncorhynchus
mykiss
rainbow trout
Oncorhynchus
mykiss
rainbow trout
Oncorhynchus
clarki
cutthroat trout
Oncorhynchus
clarki
cutthroat trout
Reference
Dobbsetal. 1996
Hamilton et al.
1990
Hamilton et al.
1990
Hilton and
Hodson 1983:
Hicks etal. 1984
Hilton etal. 1980
Holm 2000;
Holm et al.
2003
Kennedy et al.
2000
Hardy, R.W. 2002
Exposure route
dietary and
waterborne
(lab)
dietary
(lab)
dietary
(lab)
dietary
(lab)
dietary
(lab)
dietary and
waterborne
(field Luscar
River, Alberta)
dietary and
waterborne (field
- Fording River,
BC)
dietary
(lab)
Selenium form
algae exposed to SeVI
in water, algae then
fed to rotifers
Se-laden mosquitofish
from San Luis Drain,
CA
Mosquitofish spiked
with seleno-DL-
methionine
sodium selenite in
food preparation
sodium selenite in
food preparation
not determined
not determined
selenomethionine in
food preparation
Toxicological endpoint
EC20 for rotifer dry
weight after 4 d
EC20 for juvenile growth
EC20 for juvenile growth
MAT C for juven ile
growth;
nephroc alcinosis
MAT C for juven ile
survival and g rowth
2000 study: chronic
value for embryo krval
deformities
2001 study :EC20 for
craniofacial deformities
NOAEC for
embryo/larval
deformities and
mortality
NOAEC for
embryo/larval
deformities
Chronic value,
Hg/g dwa
42.36
15.74
(juvenile tissue)
10.47
(juvenile tissue)
11.65b
(juvenile tissue)
19.16b
(juvenile tissue)
5.79C
(parent tissue)
5.85C
(parent tissue)
>10.92C
(parent tissue)
>9.37
(parent tissue)
SMCV
Hg/g dw
42.36
12.84
9.32
>10.12
GMCV
Hg/g dw
42.36
10.66
78 Draft November 12, 2004
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Species
Salvelinus
fontinalis
brook trout
Pimephales
promelas
fathead minnow
Pimephales
promelas
fathead minnow
Pimephales
promelas
fathead minnow
Pimephales
promelas
fathead minnow
Catostomus
latipinnis
flannelmouth
sucker
Xyrauchen
texanus razorback
sucker
Reference
Holm 2002;
Holm et al.
2003
Bennett et al.
1986
Ogle and Knight
1989
Dobbs et al. 1996
Schultz and
Hermanutz 1990
Beyers and
Sodegren2001a
Beyers and
Sodegren2001a
Exposure route
dietary and
waterborne
(field Luscar
River, Alberta)
dietary
(lab)
dietary
(lab)
dietary and
waterborne
(lab)
dietary and
waterborne
(mesocosm -
Monticello)
dietary and
waterborne (lab)
dietary and
waterborne (lab)
Selenium form
not determined
algae expo sed to
selenite then fed to
rotifers which were
fed to fish
mix of 25,50, and 25
percent selenate,
selenite, and seleno-L-
methionine in food
preparation
algae expo sed to
selenate in water then
fed to rotifers which
were fed to fish
selenite add ed to
artificial streams
which entered food
web and provided
dietary exposure
water: selenate;
diet: algae exposed to
selenate in water then
fed to rotifers which
were fed to fish
water: selenate;
diet: algae exposed to
selenate in water then
fed to rotifers which
were fed to fish
Toxicological endpoint
2000 study: chronic
value for craniofacial
deformities
2001 study: chronic
value for finfold
deformities
Chronic value for larval
growth
MATC for pre-spawning
adult growth
LOAEC for larval fish
dry weight after 8 d
LOAEC for larval
edema and lordo sis
NOAEC for survival and
growth
NOAEC for survival and
growth
Chronic value,
ug/g dwa
13.2C
(parent tissue)
12.4C
(parent tissue)
51.40d
(larval tissue)
5.961d
(pre-spawning adult
tissue)
<73d
(larval tissue)
<18.21e
(parent tissue)
>10.2
(larval tissue)
>12.9
(larval tissue)
SMCV
Hg/g dw
12.8
<18.21
>10.2
>23.28
GMCV
Hg/g dw
12.8
<18.21
>10.2
>23.28
79 Draft November 12, 2004
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Species
Xyrauchen
texanus razorback
sucker
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Reference
Beyers and
Sodegren2001b
Brysonetal. 1984
Bryson et al.
1985a
Bryson et al.
1985b
Gillespie and
Baumann 1986
Coyleetal. 1993
Lemly 1993a
Lemly 1993a
Exposure route
dietary and
waterborne (lab)
dietary and
waterborne (field
- Hyco
Reservoir, NC)
dietary and
waterborne (field
- Hyco Reservoir,
NC)
dietary and
waterborne (field
- Hyco Reservoir,
NC)
dietary and
waterborne (field
- Hyco Reservoir,
NC)
dietary and
waterborne (lab)
dietary and
waterborne (lab)
dietary and
waterborne (lab)
Selenium form
water: site waters;
diet: algae exposed to
site water then fed to
rotifers which were
fed to fish
not determined
not determined
not determined
not determined
diet: seleno-L-
methionine
water: 6:1
selenate:selenite
diet: seleno-L-
methionine
water: 1 : 1
selenate:selenite
diet: seleno-L-
methionine
water: 1 : 1
selenate:selenite
Toxicological endpoint
NOAEC for survival and
growth
LOAEC for larval
mortality
Chronic value for swim-
up larvae
NOAEC for swim-up
larvae
Chronic value for larval
survival
EC 20 for larval survival
LOAEC for juvenile
mortality at4°C
NOAEC for juvenile
mortality at 20°C
Chronic value,
ug/g dwa
>42
(larval tissue)
<59.92c'd
(parent tissue)
<43.70c'd
>20.29c'd
(parent tissue)
>5.45c>d
(parent tissue)
<28.20d
(larval tissue); or
<21.47d'e
(parent tissue)
8.954
(parent tissue -
females only)
<7.91
(juvenile tissue)
>6.0d
(juvenile tissue)
SMCV
Hg/g dw
9.50
GMCV
Hg/g dw
9.50
80 Draft November 12, 2004
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Species
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Lepom is
macrochirus
bluegill
Centrarchidae
(9 species)
Morone saxitilis
striped bass
Reference
Hermanutz et al.
1996
Bryson et al.
1985b
Cleveland et al.
1993
Hermanutz et al.
1996
Lemly 1993b
Coughlan and
Velte 1989
Exposure route
dietary and
waterborne
(mesocosm -
Monticello)
dietary
dietary
dietary
(mesocosm -
Monticello)
dietary and
waterborne (field
- Belews Lake,
NC)
dietary
(lab)
Selenium form
selenite added to
artificial streams
which entered food
web and provided
dietary exposure
seleno-DL-cysteine
seleno-L-methionine
selenite originally
added to artificial
streams which entered
food web and
provided dietary
exposure
not determined
Se-laden shiners from
Belews Lake,NC
Toxicological endpoint
MATC for larval
survival, edema, lordosis
and hemorrhaging Study
II
NOA EC for juvenile
growth
NOA EC for juvenile
survival
NOAEC for larval
survival, edema, lordosis
and hemorrhaging Study
III
EC20 for deformities
among juveniles and
adults
LOAEC for survival of
yearling bass
Chronic value,
ug/g dwa
12.12
(parent tissue)
>3.74d
(juvenile tissue)
>13.4d
(juvenile tissue)
>17.35d
(parent tissue)
44.57
(juvenile and adult
tissue)
<14.75C
(juvenile tissue)
SMCV
Hg/g dw
NA
<14.75
GMCV
Hg/g dw
NA
<14.75
All chronic values reported in this table are based on the measured or estimated (see footnotes below) concentration of selenium in whole body tissue.
Estimated using the equation III.
Estimated using the equation I.
Chronic value not used in SMCV calculation (see text).
Estimated using the equation II.
81
Draft November 12, 2004
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National Criteria
The available data for selenium, evaluated in accordance with EPA's guidelines for deriving aquatic life
criteria (Stephan et al. 1985) indicate that, except possibly where an unusually sensitive species is
important at a site, freshwater aquatic life should be protected if the following conditions are satisfied.
A. The concentration of selenium in whole-body fish tissue does not exceed 7.91 (ig/g dw (dry weight).
This is the chronic exposure criterion. In addition, if whole-body fish tissue concentrations exceed
5.85 (ig/g dw during summer or fall, fish tissue should be monitored during the winter to determine
whether the selenium concentration exceeds 7.91 (ig/g dw.
B. The 24-hour average concentration of total recoverable selenium in water seldom (e.g., not more than
once in three years) exceeds 258 (ig/L for selenite, and likewise seldom exceeds the numerical value
given by exp(0.5812[ln(sulfate)]+3.357) for selenate. These are the acute exposure criteria. At an
example sulfate concentration of 100 mg/L, the 24-hour average selenate concentration should not
exceed 417 (ig/L.
The available data for selenium, evaluated as above, indicate that saltwater aquatic life should likewise
be protected from acute effects of selenium if the 24-hour average concentration of selenite seldom
exceeds 127 (ig/L. Because selenium might be as chronically toxic to saltwater fishes as it is to
freshwater fishes, the status of the fish community should be monitored if selenium exceeds 5.85 (ig/g dw
in summer or fall or 7.91 (ig/g dw during any season in the whole-body tissue of salt water fishes.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983b), a water quality criterion for
aquatic life has regulatory force only after it as been adopted in a State water quality standard. Such a
standard specifies a criterion for a pollutant that is consistent with a particular designated use. With the
concurrence of the U.S. EPA, States designate one or more uses for each body of water or segment
thereof and adopt criteria that are consistent with the uses (U.S. EPA 1983c, 1987b). In each standard, a
State may adopt the national criterion (if one exists), or an adequately justified state-specific or site-
specific criterion.
Criterion concentrations, durations of averaging periods, and frequencies of allowed excursions may be
established on a state-specific or site-specific basis (U.S. EPA 1983c, U.S. EPA 1985c). Because the
82 Draft November 12, 2004
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chronic criterion is tissue-based for selenium, the averaging period only applies to the acute criterion,
which is defined as a 24-hour average, based on the speed at which effects may occur in the toxicity tests
used for its derivation. Implementation guidance on using criteria to derive water quality-based effluent
limits is available in U.S. EPA (1985cand 1987b).
83 Draft November 12, 2004
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APPENDIX A
INFORMATION USED IN THE SULFATE CORRECTION OF
SELENATE ACUTE TOXICITY
A-1 Draft November 12, 2004
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Table A-l. Degrees of freedom (df), coefficients of determination (-2), slopes and respective
confidence intervals (CI) for regressions of the natural logarithm of selenate LC50% on the
natural logarithm of sulfate concentration. The "Common regression" combines regression
lines for individual species into a single model (Zar 1999), its slope is computed as in
analysis of covariance. The "Total regression" estimates a linear function for all points,
irrespective of taxa.
Species df r2 Slope 95% CI
Fathead Minnow 14 0.83 0.48 [0.35,0.60]
Chinook Salmon 3 0.87 0.49 [0.14,0.83]
Gammarus pseudolimnaeus 5 0.61 0.86 [0.07, 1.66]
Hyalellaazteca 4 0.39 0.19 [-0.14,0.51]
Daphniamagna 4 0.92 0.87 [0.52,1.22]
Ceriodaphnia dubia 11 0.84 0.70 [0.50,0.91]
"Common regression" 46 0.65 0.58 [0.45,0.71]
"Total regression" 51 0.36 0.76 [0.48,1.04]
A-2 Draft November 12, 2004
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Table A-2. Data used in the regressions of the natural logarithm of selenate acute values on the
natural logarithm of sulfate concentrations.
Species
Hydra
Hydra sp.
Leech
Nephelopsis obscura
Snail
Aplexa hypnorum
Cladoceran
Ceriodaphnia dubia
Ceriodaphnia dubia
Ceriodaphnia dubia
Cladoceran
Daphnia magna
Daphnia magna
Daphnia magna
Daphnia magna
Daphnia magna
Daphnia magna
Daphnia pulex
Daphnia pulex
Daphnia pulex
Daphnia pulicaria
Amphipod
Gammarus lacustris
Gammarus pseudolimnaeus
Gammarus pseudolimnaeus
Gammarus pseudolimnaeus
Age/ Size Data Source
adult Brooke et al. 1985
adult Brooke et al. 1985
Brooke et al. 1985
<24 hr Brix et al. 2001a,b
Brixetal. 200 la,b
GLEC 1999
Dunbaretal. 1983
Boyum 1984
Brooke et al. 1985
Ingersoll et al. 1990
Ingersoll et al. 1990
Maieretal. 1993
<24 hr Brix et al. 2001a,b
Brixetal. 200 la,b
GLEC 1999
Boyum 1984
8-12 mm Brix et al. 2001a,b
adult Brooke et al. 1985
Brooke 1987
GLEC 1998
[Sulfate]
(fig/L)
12000
12000
12000
52000
55000
25000
163000
22000
12000
41000
68000
82000
54000
38000
25000
22000
120000
12000
12000
25000
LC50 or
EC50
(US/L)
7,300
442,000
193,000
1,969
1,864
376
5,300
1,010
570
2,560
4,070
2,840
10,123
8,111
1,528
246
3,054
75
57
1,180
Adjusted
LC50
25031.02
1515577
661779.1
2879.368
2638.398
841.5682
3989.863
2434.939
1954.477
4298.133
5092.556
3187.186
14482.21
14232.89
3419.99
593.0643
2746.951
257.168
195.4477
2641.092
A-3
Draft November 12, 2004
-------
Species Age/ Size
Gammarus pseudolimnaeus
Gammarus pseudolimnaeus
Gammarus pseudolimnaeus
Gammarus pseudolimnaeus
Amphipod
Hyalella azteca
Hyalella azteca
Hyalella azteca
Hyalella azteca
Hyalella azteca
Hyalella azteca
Hyalella azteca
Midge
Chironomus decorus 4th instar
Midge
Paratanytarsus parthenogeneticus 3rd instar
Coho salmon
Oncorhynchus kisutch 0.5 g
Oncorhynchus kisutch 1.7 g
Oncorhynchus kisutch alevin
Oncorhynchus kisutch juvenile
Oncorhynchus tshawytscha (0.7 g
Oncorhynchus tshawytscha 0.5 g
Oncorhynchus tshawytscha 1.6g
Oncorhynchus tshawytscha
Oncorhynchus tshawytscha eyed egg
Oncorhynchus tshawytscha alevin
Data Source [Sulfate]
(fig/L)
GLEC 1998
GLEC 1998
GLEC 1998
GLEC 1999
Adams 1976
Brasher and Ogle 1993
Brixetal. 2001a,b
GLEC 1998
GLEC 1998
GLEC 1998
GLEC 1998
Maier and Knight 1993
Brooke et al. 1985
Hamilton and Buhl 1990b
Hamilton and Buhl 1990b
Buhl and Hamilton 1991
Buhl and Hamilton 1991
Hamilton and Buhl 1990b
Hamilton and Buhl 1990b
Hamilton and Buhl 1990b
Hamilton and Buhl 1990b
Hamilton and Buhl 1990b
Hamilton and Buhl 1990b
125000
367000
635000
25000
-
13000
55000
40000
125000
367000
822000
27000
12000
185000
291000
41000
41000
185000
185000
291000
291000
LC50 or
EC50
(US/L)
2,870
3,710
3,270
2,191
760
1,031
1,428
2,480
1,350
1,540
3,580
23,700
20,000
32,500
39,000
158,422
30,932
121,000
100,000
180,000
134,000
Adjusted
LC50
2520.927
1742.628
1116.855
4903.925
-
3374.516
2021.262
4224.001
1185.802
723.3552
1052.407
50725.32
68578.14
22730.56
20963.42
265983.9
51933.53
84627.63
69940.19
96754.25
72028.17
47000>552,000
47000>176,640
A-4
Draft November 12, 2004
-------
Species
Age/ Size Data Source
[Sulfate] LC50 or Adjusted
(ug/L) EC50 LC50
(ug/L)
Oncorhynchus tshawytscha
Rainbow trout
Oncorhynchus mykiss
Oncorhynchus mykiss
Oncorhynchus mykiss
Oncorhynchus mykiss
Arctic grayling
Thymallus arcticus
Thymallus arcticus
Fathead minnow
Pimephales promeles
Pimephales promeles
Pimephales promeles
Pimephales promelas
Pimephales promelas
Pimephales promelas
Pimephales promelas
Pimephales promelas
Pimephales promelas
Colorado squawfish
Ptychocheilus lucius
Ptychocheilus lucius
Ptychocheilus lucius
Ptychocheilus lucius
Ptychocheilus lucius
Ptychocheilus lucius
0.31 g Hamilton and Buhl 1990b 47000 62,900 97548.09
juvenile Brooke et al. 1985
alevin Buhl and Hamilton 1991
juvenile Buhl and Hamilton 1991
Spehar1986
12000 24,000 82293.77
41000 196,460 329848.1
41000 13,501 22667.61
12000 47,000 161158.6
alevin Buhl and Hamilton 1991 41000 41,800 70180.45
juvenile Buhl and Hamilton 1991 41000 75,240 126324.8
juvenile
fry
Adams 1976
Adams 1976
Adams 1976
Brooke et al. 1985
Spehar1986
GLEC 1998
GLEC 1998
GLEC 1998
GLEC 1998
Hamilton 1995
0.4-1. Ig Hamilton 1995
juvenile
1.7g Hamilton 1995
juvenile
larva Buhl and Hamilton 1996
juvenile Buhl and Hamilton 1996
0.024-0.047 Hamilton and Buhl 1997a
11,800
11,000
12,500
12000 2,300 7886.486
12000 5,500 18858.99
24000 6,210 14233
160000 10,800 8218.538
474000 18,000 7286.649
906000 42,100 11695.65
164000 27,588 20694.67
164000 119,548 89676.92
164000 138,358 103786.9
174000 13,580 9842.351
174000 42,780 31005.58
97000 88,000 89571.65
A-5
Draft November 12, 2004
-------
Species
Bonytail
Gila elegans
Gila elegans
Gila elegans
Gila elegans
Gila elegans
Age/ Size
fry
1-lg
juvenile
2.6 g
juvenile
larva
juvenile
Data Source [Sulfate] LC50 or
(ug/L) EC50
fus/L)
Hamilton 1995
Hamilton 1995
Hamilton 1995
Buhl and Hamilton 1996
Buhl and Hamilton 1996
164000
164000
164000
174000
174000
22,990
102,828
90,706
14,570
24,010
Adjusted
LC50
17245.56
77134.7
68041.58
10559.87
17401.68
Razorback sucker
Xyrauchen texanus
Xyrauchen texanus
Xyrauchen texanus
Xyrauchen texanus
Xyrauchen texanus
Xyrauchen texanus
Flannelmouth sucker
Catostomus latipinnis
Channel catfish
Ictalurus punctatus
Bluegill
Lepomis macrochirus
fry
Hamilton 1995
Hamilton 1995
Hamilton 1995
Buhl and Hamilton 1996
juvenile Buhl and Hamilton 1996 174000
0.006-0.042 Hamilton and Buhl 1997a
0.9 g
juvenile
2.0 g
juvenile
larva
164000 20,064 15050.67
164000 15,048 11288.00
164000 10,450 7838.892
174000 13,910 10081.52
7,620 5522.733
97000 15,900 16183.97
12-13 days Hamilton and Buhl 1997b 97000 26,900 27380.43
juvenile Brooke et al. 1985
juvenile Brooke et al. 1985
12000 66,000 226307.9
12000 63,000 216021.1
A-6
Draft November 12, 2004
-------
APPENDIX B
TOXICITY OF SELENIUM TO AQUATIC PLANTS
B-1 Draft November 12, 2004
-------
Toxicity to Aquatic Plants
Selenite
Data are available on the toxicity of selenite to 13 species of freshwater algae and plants (Table B-l).
Results ranged from an LQ0 of 70,000 (ig/L for the green alga, Chlorella ellipsoidea (Shabana and El-
Attar 1995) to 522 (ig/L for incipient inhibition of the green alga,Scenedesmus quadricauda (Bringmann
and Kuhn 1977a, 1978a,b, 1979, 1980b). Foe and Knight (Manuscript) found that 75 (ig/L decreased the
dry weight ofSelenastrum capricornutum (Table F-l). Wehr and Brown (1985) reported that 320 (ig/L
increased the growth of the alga Chrysochromulina breviturrita. Thus, the sensitivities of freshwater algae
to selenite cover about the same range as the acute and chronic sensitivities of freshwater animals.
The 96-hr EC50 for the saltwater diatom, Skeletonema costatum, is 7,930 (ig/L, based on reduction in
chlorophyll a (Table B-l). Growth of Chlorella sp., Platymonas subcordiformis, and Fucus spiralis
increased at selenite concentrations from 2.6 to 10,000 (ig/L (Table F-l). Other marine algae exposed to
selenite from 14 to 60 days had no observed effect concentrations (NOAEC) that ranged from 1,076 to
107,606 (ig/L. These data suggest that saltwater plants will not be adversely affected by concentrations of
selenite that do not affect saltwater animals.
Selenate
Growth of several species of green algae were affected by concentrations ranging from 100 to 40,000 (ig/L
(Table B-l). Blue-green algae appear to be more tolerant to selenate with 1,866 (ig/L being the lowest
concentration reported to affect growth (Kiffney and Knight 1990). Kumar (1964) found that a blue-green
alga developed and lost resistance to selenate. The difference in the sensitivities of green and blue-green
algae to selenate might be of ecological significance, particularly in bodies of water susceptible to nuisance
algal blooms. For example, Patrick et al. (1975) reported that a concentration of 1,000 (ig/L caused a
natural assemblage of algae to shift to a community dominated by blue-green algae.
The saltwater coccolithophore, Cricosphaera elongata, had reduced growth when exposed to 41,800 (ig/L
selenate for 14 days (Boisson et al. 1995). Seven other saltwater algal species investigated by Wong and
B-2 Draft November 12, 2004
-------
Oliveira (1991a) exhibited NOEC growth values that ranged from 1,043 to 104,328 (ig/L. At 10,000
(ig/L, selenate is lethal to four species of saltwater phytoplankton and lower concentrations increase or
decrease growth (Table F-l). Wheeler et al. (1982) reported that concentrations as low as 10 (ig/L reduced
growth of Porphyridium cruentum (Table F-l).
Although selenite appears to be more acutely and chronically toxic than selenate to most aquatic animals,
this does not seem to be true for aquatic plants. Selenite and selenate are about equally toxic to the
freshwater algae Anabaena cylindrica, Anabaena flos-aquae, Anabaena variabilis, Anacystis nidulans,
and Scenedesmus dimorphus (Kiffney and Knight 1990; Kumar and Prakash 1971; Moede et al. 1980) and
the saltwater algae Agemenellum quadroplicatum, Chaetoceros vixvisibilis and Amphidinium carterae
(Wong and Oliveira 199la). The two oxidation states equally stimulated growth ofChrysochromulina
breviturrita (Wehr and Brown 1985). On the other hand, selenate is more toxic than selenite to the
freshwater Selenastrum capricornutum (Richter 1982; Ibrahim and Spacie 1990) and the saltwater
Chorella sp., Platymonas subcordiformis and Nannochloropsis oculata (Wheeler et al. 1982; Wong and
Oliveira 1991a). In addition, Fries (1982) found that growth of thalli of the brown macroalga^Hczw
spiralis, was stimulated more by exposure to selenite at 2.605 (ig/L than to the same concentration of
selenate.
A Final Plant Value, as defined in the Guidelines, cannot be obtained because no test in which the
concentrations of selenite or selenate were measured and the endpoint was biologically relevant has been
conducted with an important aquatic plant species.
B-3 Draft November 12, 2004
-------
Table B-l.
Toxicity of Selenium to Aquatic Plants
Species
Green alga,
Chlorella vulgaris
Green alga,
Chlorella
ellipsoidea
Green alga,
Scenedesmus
dimorphus
Green alga,
Scenedesmus
quadricauda
Green alga,
Scenedesmus
quadricauda
Green alga,
Selenastrum
capricornutum
Green alga,
Selenastrum
capricornutum
Blue-green alga,
Anabaena
constricta
Blue-green alga,
Anabaena
cylindrica
Blue-green alga,
Anabaena flos-
aquae
Blue-green alga,
Anabaena
variabilis
Blue-green alga,
Anacystis
nidulans
Blue-green alga,
Microcystis
aeruginisa
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as Duration
CaCO,) (days) Effect
FRESHWATER SPECIES
Selenium (IV)
90-120 Reduced
growth
7 EC50
14 Reduced
growth
8 Incipient
inhibition
8 Incipient
inhibition
4 EC50
6 EC50
7 EC50
14 Reduced
growth
10 Reduced
chlorophyll a
6-18 LC50
10-18 LC50
8 Incipient
inhibition
Concentration
(ue/L)a
5,480
70,000
24,000
522
2,500
2,900
65,000
67,000
24,000
1,866
15,000b
30,000b
9,400
(9,300)
Reference
De Jong 1965
Shabana and El-
Attar 1995
Moede et al.
1980
Bringmann and
Kuhn 1977a;
1978a,b; 1979;
1980b
Bringmann and
Kuhn 1959a
Richter 1982
Ibrahim and
Spacie 1990
Shabana and El-
Attar 1995
Moede et al.
1980
Kiffney and
Knight 1990
Kumar and
Prakash 1971
Kumar and
Prakash 1971
Bringmann and
Kuhn 1976;
1978a,b
B-4
Draft November 12, 2004
-------
Table B-l.
Toxicity of Selenium to Aquatic Plants (cont.)
Species
Alga,
Euglena gracilis
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Green alga,
Ankistrodesmus
falcatus
Green alga,
Scenedesmus
dimorphus
Green alga,
Scenedesmus
obliquus
Green alga,
Selenastrum
capricornutum
Green alga,
Selenastrum
capricornutum
Green alga,
Selenastrum
capricornutum
Blue-green alga,
Anabaena
cylindrica
Blue-green alga,
Anabaena flos-
aquae
Blue-green alga,
Anacystis
nidulans
Chemical
-
-
Sodium
selenite
Sodium
selenite
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Hardness
(mg/L as Duration
CaCO,) (days) Effect
1 5 Reduced
growth
4 EC50
14 EC50
(mult, rate)
14 NOEC
(mult, rate)
Selenium (VI)
14 Did not
reduce
growth
14 Reduced
growth
14 Reduced
growth
14 Reduced
growth
4 EC50
6 EC50
14 Reduced
growth
10 Reduced
chlorophyll a
6-18 EC50
Concentration
(us/L)a
5,920
2,400
3,500
800
10
22,100
100
300
199
<40,000
22,100
1,866
39,000b
Reference
Bariaud and
Mestre 1984
Wang 1986
Jenner and
Janssen-
Mommen 1993
Jenner and
Janssen-
Mommen 1993
Vocke et al.
1980
Moede et al.
1980
Vocke et al.
1980
Vocke et al.
1980
Richter 1982
Ibrahim and
Spacie 1990
Moede et al.
1980
Kiffney and
Knight 1990
Kumar and
Prakash 1971
B-5
Draft November 12, 2004
-------
Table B-l.
Toxicity of Selenium to Aquatic Plants (cont.)
Species
Chemical
Hardness
(mg/L as
CaCOl
Duration
(days) Effect
Concentration
(lig/L)a Reference
Blue-green alga,
Anabaena
viriabilis
Blue-green alga,
Microcoleus
vaginatus
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
10-18 EC50
17,000b Kumar and
Prakash 1971
14
14
14
Reduced
growth
EC50
(mult, rate)
NOEC
(mult. Rate)
10,000
11,500
>2,400
Vocke et al.
1980
Jenner and
Janssen-
Mommen 1993
Jenner and
Janssen-
Mommen 1993
B-6
Draft November 12, 2004
-------
Table B-l.
Toxicity of Selenium to Aquatic Plants (cont.)
Species
Green alga,
Dunaliella
tertiolecta
Cyanophyceae alga,
Agemenellum
quadruplicatum
Diatom,
Chaetoceros
vixvisibilis
Diatom,
Skeletonema
costatum
Coccolithophore,
Cricosphaera
elongata
Dinoflagellate,
Amphidinium
carterae
Dinoflagellate,
Peridinopsis borgei
Eustigmatophyceae
alga,
Nannochloropsis
oculata
Pyrmnesiophyceae
alga,
hochrysis galbana
Pyrmnesiophyceae
alga,
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acidc
Sodium
selenite
Sodium
selenite
Selenium
oxide
Sodium
selenite
Sodium
selenite
Sodiun
selenite
Salinity Duration
(g/kg) (days) Effect
SALTWATER SPECIES
Selenium (IV)
60 NOEC growth
60 NOEC growth
60 NOEC growth
4 EC50
(reduction in
chlorophyll a)
14 Reduced growth
60 NOEC growth
70-75 Maximum
growth
60 NOEC growth
60 NOEC growth
60 NOEC growth
Concentration
(ug/L)a
1,076
10,761
1,076
7,930
4,570
10,761
0.01-0.05
107,606
1,076
1,076
Reference
Wong and
Oliveira 199 la
Wong and
Oliveira 199 la
Wong and
Oliveira 199 la
U.S. EPA 1978
Boisson et al.
1995
Wong and
Oliveira 199 la
Lindstrom 1985
Wong and
Oliveira 199 la
Wong and
Oliveira 199 la
Wong and
Oliveira 199 la
Pavlova lutheri
B-7
Draft November 12, 2004
-------
Table B-l.
Toxicity of Selenium to Aquatic Plants (cont.)
Species
Chemical
Salinity Duration
(days) Effect
Concentration
(lig/L)a Reference
Green alga,
Dunaliella
tertiolecta
Cyanophyceae alga,
Agemenellum
quadruplicatum
Diatom,
Chaetoceros
vixvisibilis
Coccolithophore,
Cricosphaera
elongata
Dinoflagellate,
Amphidinium
carterae
Eustigmatophyceae
alga,
Nannochloropsis
oculata
Pyrmnesiophyceae
alga,
Isochrysis galbana
Pyrmnesiophyceae
alga,
Pavlova lutheri
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Selenium (VI)
60 NOEC growth 104,328 Wong and
Oliveira 199 la
60 NOEC growth 10,433 Wong and
Oliveira 199 la
60 NOEC growth 1,043 Wong and
Oliveira 199 la
14 Reduced growth 41,800 Boissonetal.
1995
60 NOEC growth 10,433 Wong and
Oliveira 199 la
60 NOEC growth 10,433 Wong and
Oliveira 199 la
60 NOEC growth 10,433 Wong and
Oliveira 199 la
60 NOEC growth 104,328 Wong and
Oliveira 199 la
a Concentration of selenium, not the chemical.
b Estimated from published graph.
c Reported by Barrows et al. (1980) in work performed under the same contract.
B-8
Draft November 12, 2004
-------
APPENDIX C
BIOCONCENTRATION AND BIOACCUMUALTION OF SELENIUM
C-l DraftNovemberl2,2004
-------
Bioconcentration and Bioaccumulation
Laboratory-Derived
Bioconcentration factors (BCFs) for selenium(IV) that have been obtained with freshwater species range
from a low of 2 for the muscle of rainbow trout to 470 for the bluegill sunfish (Table C-l). Adams (1976)
studied both uptake and elimination of selenium 75 by fathead minnows exposed to mean concentration of
12, 24, and 50 (ig/L in the water. He found that concentrations in whole fish and in individual tissues
increased at a rapid rate during the first 8 days and then at a slower rate for the next 88 days. Steady-state
was approached, but not reached, after 96 days. The highest concentrations were found in viscera.
Elimination of selenium was curvilinear and became asymptotic with the time axis after 96 days.
Elimination was most rapid from the viscera with a half-life of 5.1 days, but the half-life of selenium in
other tissues was greater than 50 days.
Adams (1976) also conducted uptake studies with rainbow trout exposed for 48 days to selenium(IV) at
water concentrations ranging from 310 to 950 (ig/L. Some of the trout died, and concentrations were
somewhat higher in dead fish than in survivors. As with the fathead minnow, the viscera contained more
selenium than gill or muscle. Based on his tests with the two fish species, Adams (1976) concluded that
there was an inverse relationship between BCF and the concentration of selenium(IV) in water.
Gissel-Nielsen and Gissel-Nielsen (1978) exposed juvenile rainbow trout ( Oncorhynchus my kiss) to
waterborne selenium(IV) over a four week period. Exposure to selenium at 100 (ig/L raised the selenium
concentration in fish to 2.3 ± 0.02 (ig/g dw, without increasing mortality, and steady-state conditions were
shown to have been achieved.
Hodson et al. (1980) exposed rainbow trout to selenium(IV) from fertilization until 44 weeks post-hatch.
At 53 (ig/L selenium in the water, the BCF ranged from 8 L/kg for whole-body to 240 L/kg for liver. They
concluded that selenium in tissues did not increase in proportion to selenium(IV) in water.
Hunn et al. (1987) exposed rainbow trout in a flow-through system to waterborne selenium(IV) for 90
days. The selenium concentration in the water where significant effects were not observed was 21 (ig/L
and the corresponding whole-body tissue level was 0.64 (ig/g dw, the data yielding a BCF value of 30.5
L/kg.
C-2 DraftNovember 12,2004
-------
Barrows et al. (1980) exposed bluegills to selenious acid for 28 days. They reported a maximum BCF in
the whole fish of 20 L/kg and a half-life of between 1 and 7 days. If bluegills bioconcentrate selenium in
the same manner as the rainbow trout used by Adams (1976), the 28-day exposure might not have been
long enough to reach steady-state.
Lemly (1982) exposed bluegills and largemouth bass to 10 (ig of selenium/L for 120 days to determine the
effect of hardness and temperature on uptake and elimination. For bluegills, the geometric mean whole-
body BCF at 20° and 30°C was 452 L/kg. For largemouth bass in similar tests, the BCF was 295 L/kg.
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 the amount of selenium accumulated in
the tissues after 90 days, although earlier values were influenced. After 30 days in clean water, selenium
concentrations remained unchanged in spleen, liver, kidney, and white muscle, but the half-life for selenium
in gills and erythrocytes was less than 15 days.
Besser et al. (1993) measured the aqueous bioaccumulation of both waterborne selenium(IV) and
selenium(VI) by bluegill over a 30-day period. Selenium concentrations were monitored radiometrically
with 75 Se- labeled compounds. Bluegills concentrated selenium about equally from both inorganic species
and demonstrated similar aqueous selenium uptake rate constants (about 3 per day at 10 (ig of selenium/L).
A kinetic uptake-depuration model was used to estimate BCFs. Estimated BCFs for both selenium(TV)
and selenium(VI) derived from the data were 56 L/kg.
Bertram and Brooks (1986) exposed adult fathead minnows to sodium selenate in water, in food, and in
food and water together. The food was specially prepared by raising algae in a medium containing
selenium(VI), feeding the algae to daphnids, mixing the exposed daphnids with unexposed daphnids,
dewatering to form a "cake", and freezing for storage. Uptake of selenium(VI) from water (without the
additional selenium in food) reached steady-state within 28 days. The whole-body BCFs ranged from 21 to
52 L/kg and decreased as the concentration in water increased (Table C-l). Uptake of selenium(VI) from
food alone or from food and water together did not reach steady-state in 8 and 11 weeks, respectively. The
uptake of selenium from food and water were additive.
Besser et al. (1993) also determined BCF values for algae and Daphnia magna exposed separately to
waterborne selenium(IV) and selenium(VI). At 10 (ig of selenium/L, the BCFs calculated for algae were
C-3 DraftNovember 12,2004
-------
1440 L/kg for selenium(IV) and 428 L/kg for selenium(VI). In these laboratory simulated food web studies
(waterborne selenium to algae; algae to Daphnia; and Daphnia to bluegills) concentration factors (CFs) for
the transfer of selenium from algae to Daphnia and Daphnia to bluegill (0.61 and 0.51 L/kg, respectively)
were also determined (Table C-2). Using the BCF and CF data, one can calculate an estimated BAF for
bluegill for this laboratory food chain. An estimated BAF value of 550 L/kg was calculated for a
waterborne exposure of 10 (ig/L of 1:1 selenite:selenate to the algae- Daphnia - bluegill web.
A three-trophic level food chain experiment consisting of the alga, Chlorella vulgaris, the rotifer,
Brachionus calyciflorus, and the fathead minnow, Pimephales promelas was conducted by Dobbs et al.
(1996). The three species were exposed to selenium(VI) for 25 days in a three-trophic level system
whereby the organisms were linked in a continuous flow-through system in separate vessels, with each
organism feeding on the trophic level below it. These organisms were continuously exposed for 25 days to
either 0, 110.3, 207.7 or 396.1 (ig of total recoverable selenium/L from selenium(VI) in natural creek water
supplemented with nutrients to sustain algal growth. Algal population growth, rotifer standing crop, and
fathead minnow growth were reduced at 207.7, 110.3 and 110.3 \\%TL, respectively, after the 25-day
exposure. Bioconcentration factors were found to be dependent on the species, treatment level and length of
exposure, and they ranged between 100 and 1,000 L/kg.
Hamilton et al. (2000) exposed, separately, swim-up larvae of razorback sucker ( Xyrauchen texanus) and
bonytail (Gila elegans) to waterborne selenium in a simulated Green River, Utah water formulation. The
selenium was 6:1 selenate:selenite, and the measured ambient or base level was 76 (ig/L in the razorback
exposure and 73 (ig/L in the bonytail exposure. A flow-through system was utilized, and a 90-day partial
life-cycle chronic toxicity study monitoring growth, behavior and mortality was conducted. No chronic
effects were observed in tests conducted at base level. Fligher than ambient concentrations were studied
also, but were not selected for use in the BCF derivation due to either observed chronic effects or
abnormally high concentrations of selenium and other metals in the test waters. At 90 days, the whole-
body tissue levels of selenium were 3.2 (ig/g dw in the razorback and 2.2 (ig/g dw in the boneytail,
reflecting BCF values of 42 and 30 L/kg, respectively.
C-4 DraftNovemberl2,2004
-------
Field-Derived
Hermanutz et al. (1996) exposed bluegills to selenium(IV) over 221 days in outdoor experimental streams
at Monticello, MN which contained a natural food web. At the end of the 221 days in waters maintained at
a nominal selenium concentration of 2.5 (ig/L, the average whole-body fish tissue level of selenium was
4.825 (ig/g Se dw (based on a factor of 0.8 moisture content in fish tissue). The resulting BAF value was
1,930 L/kg.
Garcia-Hernandez et al. (2000) collected fish samples form October 1996 to March 1997 in a Sonora,
Mexico wetland. Dissolved selenium concentrations in the water ranged from 5 to 19 (ig/1 (median of 11
(ig/1). Median whole-body concentration of selenium was measured in Tilapia (3.0 (ig/g dw), carp (3.3
(ig/g dw), and largemouth bass (5.1 (ig/g dw). Resulting BAF values were 273, 300, and 464 L/kg,
respectively.
Kennedy et al. (2000) collected spawning age (3-6 years) cutthroat trout from the Fording River, British
Columbia in 1998. The waters of the river had an average selenium level of 13.9 (ig/L at the time of
collection. The tissue (muscle) of the trout contained 12.5 ± 7.7 (ig of selenium/g dw. Utilization of these
values provides a field derived muscle BAF of 899 L/kg.
Mason et al. (2000) collected biota in two streams (Blacklick Run and Herrington Creek) in western
Maryland in October 1997, April 1998, and July 1998. Water samples were collected for analysis monthly
over the duration of the study. Numerous fish species, among other organisms, were collected during each
of the sampling periods, and whole-body tissue levels of selenium were measured. In Herrington Creek, the
average water concentration of selenium was found to be 0.33 (ig/L, and the average tissue levels of
selenium in the fish were: bullhead (1.35 (ig/g dw); sucker (1.55 (ig/g dw), trout (1.94 (ig/g Se dw), and
chub (1.50 (ig/g Se dw). The resulting calculated BAF values were 4,091, 4,697, 5,879, and 4,545 L/kg,
respectively. In Blacklick Creek the average water concentration was 0.39 (ig/L, and the average tissue
levels of selenium in fish were: dace (1.79 (ig/g dw), trout (1.94 (ig/g dw), and sculpin (2.55 (ig/g dw).
Resulting BAF values were 4,590, 4,974, and 6,538 L/kg, respectively. Dry weight values were obtained
from the published wet weight data employing a 0.8 factor for fish moisture content.
C-5 DraftNovemberl2,2004
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Table C-l. Bioconcentration and Bioaccumulation of selenium by fish.
Fish Species
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout
(embryo),
Oncorhynchus
mykiss
Rainbow trout
Oncorhorynchus
mykiss
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow
(6-9 mo.),
Pimephales
promelas
Fathead minnow
(6-9 mo.),
Pimephales
promelas
Fathead minnow
(6-9 mo.),
Pimephales
promelas
Bluegill,
Lepomis
macrochirus
Selenium
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenate
Sodium
selenate
Sodium
selenate
Selenious
acid
Concentration
in Water Duration
(UB./LY (days)
LABORATORY PI
48
48
100 28
308
(post-
hatch)
21 90
96
96
10.7 56
21.5 56
43.5 56
28
Tissue
(Concentration )
7RIVED
Muscle
Whole-body
Whole-body
(2.3 ng/g )
Whole-body
(estimate)
Whole-body
(0.64 ng/g)
Muscle
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
BCFb BAFb
(L/kg) (L/kg) Reference
2 Adams 1976
10C Adams 1976
23 Gissel-Nielsen
and Gissel-
Nielsen 1978
42 Hodson
etal. 1980
30.5 Hunn
etal. 1987
11.6 Adams 1976
17.6 Adams 1976
52d Bertram and
Brooks 1986
26d Bertram and
Brooks 1986
21 d Bertram and
Brooks 1986
20 Barrows
etal. 1980
C-6
Draft November 12, 2004
-------
Table C-l continued.
Concentration
Fish Species
Bluegill,
Lepomis
macrochirus
Bluegill,
Lepomis
macrochirus
Largemouth bass,
Micropterus
salmoides
Bluegill,
Lepomis
macrochirus
Bluegill,
Lepomis
macrochirus
Razorback suker,
Xyrauchen
texanus
Bonytail,
Gila elegans
Selenium
Species
Sodium
selenite
Selenate
Sodium
selenite
Selenite
selenite:
selenate 1 : 1
selenate/
selenite f
selenate/
selenite f
in Water
(ug/L)a
10
10
10
10
10
10
10
10
10
10
10
76
73
Duration
(days)
120
120
120
120
30
120
120
120
120
30
30
90
90
Tissue
(Concentration )
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
Whole-body
(3.2 ug/g)
Whole-body
(2.2 ug/g)
BCFb BAFb
(L/kg) (L/kg) Reference
450 Lemly 1982
470
430
460
56 Besser
etal. 1993
310 Lemly 1982
300
300
270
56 Besser
etal. 1993
550e Besser
etal. 1993
42 Hamilton
et al. 2000
30 Hamilton
et al. 2000
FIELD DERIVED
Bluegill
Lepomis
macrochirus
Tilapia sp.
Carp,
Cyprinus carpio
Largemouth bass,
Micropterus
salmoides
Cutthroat trout,
Oncorhynchus
clarki
Brown bullhead,
Ictalurus
nebulosus
Selenite
Natural f
Natural f
Natural f
Natural f
Natural5
(Herrington
Creek, MD)
2.5
11
11
11
13.9
0.33
221
Field
Field
Field
Field
N/Ag (10
month
study)
Whole-body
(4.825 ug/g)
Whole-body
(3.0 ug/g)
Whole-body
( 3.3 ug/g)
Whole-body
(5.1 ug/g)
Muscle
(12.5 ug/g)
Whole-body
(1.35 ug/g)
1,930 Hermanutz
etal. 1996
273 Garcia-
Hemandez
et al. 2000
300 Garcia-
Hemandez
et al. 2000
464 Garcia-
Hemandez
et al. 2000
899 Kennedy
et al. 2000
4,091 Mason et al.
2000
C-7
Draft November 12, 2004
-------
Table C-l continued.
Fish Species
White sucker,
Catostomus
commersoni
Brook Trout,
Salvelinus
fonticnalis
Creek Chub,
Semotilus
arromaculatus
Mottled Sculpin,
Cottus bairdi
Blacknose Dace
Rhinchthus
atratulus
Brook Trout
Salvelins
fortinalus
Selenium
Natural f
(Herrington
Creek, MD)
Natural5
(Herrington
Creek, MD)
Natural5
(Herrington
Creek, MD)
Natural f
(Blacklick
Run,MD)
Natural f
(Blacklick
Run,MD)
Natural f
(Blacklick
Run,MD)
Concentration
in Water
fus/L)a
0.33
0.33
0.33
0.39
0.39
0.39
Duration
(days)
N/A (10
month
study)
N/A (10
months
study)
N/A (10
months
study)
N/A (10
months
study)
N/A (10
months
study)
N/A (10
months
study)
Tissue
(Concentration )
Whole-body
(1.55 ug/g)
Whole-body
(1.94 ug/g)
Whole-body
(1.50 ug/g)
Whole-body
(2.55 ug/g)
Whole-body
(1.79 ug/g)
Whole-body
(1.94 ug/g)
BCFb BAFb
(L/kg) (L/kg)
4,697
5,879
4,545
6,538
4,590
4,974
Reference
Mason et al.
2000
Mason et al.
2000
Mason et al.
2000
Mason et al.
2000
Mason et al.
2000
Mason et al.
2000
a Measured concentration of selenium.
b Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured concentrations of selenium in
water and in tissue (dry weight).
c Estimated from graph.
d Calculated by dividing the reported equilibrium concentration in tissue (steady-state body burden) by the average measured
concentration in water.
e Laboratory food chain: water-> algae -> daphnia -> bluegill.
f Not speciated.
g N/A not applicable.
Draft November 12, 2004
-------
Table C-2. Bioconcentration and Bioaccumulation of selenium by other aquatic organisms.
Concentration
Other Species
Selenium
Form
in Water
(ug/Ly
Duration
(days)
Tissue BCFb BAFb
(Concentration ) (L/kg) (L/kg)
Reference
LABORATORY DERIVED
Algae,
Chlamydomonas
reinhardtii
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Ephemeroptera
Heptageniidae
Ephemeroptera
Heptageniidae
Chironomidae
Chironomidae
Hydropsychidae
Selenite
Selenate
Selenate:
Selenite
1:1
Selenate:
Selenite
1:1
Selenite
Selenate
Selenite
Selenite
Natural f
(Herrington
Creek, MD)
Natural f
(Blacklick
Run,MD)
Natural f
Natural f
Selenite
Selenite
Natural
(ite/ate9:l)
10
10
156
348
10
10
2.5
10
0.33
0.39
14.5
1.58
2.5
10
32
4
4
21
21
4
4
FIELD DERIVED
221
221
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(Syr.
study)
N/A
(Syr.
study)
221
221
N/A
1440
428
Whole-body 94
(14.7 ug/g)
Whole-body 91
(31. 7 ug/g)
570e
293 e
Whole-body 1,957
(5.05 ug/g)
Whole-body 1,787
(17.30 ug/g)
Whole-body 17,600
(5.05 ug/g)
Whole-body 14,900
(5.8 ug/g)
Wholebody 1703
(24.7 ug/g)
Wholebody 6582
(10.4 ug/g)
Wholebody 1399
(3.61 ug/g)
Wholebody 1405
(13.60 ug/g)
Wholebody 969
(3.1 ug/g)
Besser et
al. 1993
Ingersoll et
al. 1990
Besser et
at. 1993
Hermanutz
etal. 1996
Mason et
al. 2000
Zhang and
Moore
1996
Hermanutz
etal. 1996
Reash et
al. 1999
C-9
Draft November 12, 2004
-------
Table C-2 Continued.
Other Species
Hydropsychidae
Astacidae
Periphyton
Bryophytes
Selenium
Form
Natural5
(Herrington
Creek, MD)
Natural f
(Blacklick
Run,MD)
Natural f
(Herrington
Creek, MD)
Natural f
(Blacklick
Run,MD)
Natural f
(Herrington
Creek, MD)
Natural f
(Blacklick
Run,MD)
Natural f
(Herrington
Creek, MD)
Natural f
(Blacklick
Run,MD)
Concentration
in Water
(ug/Ly
0.33
0.39
0.33
0.39
0.33
0.39
0.33
0.39
Duration
(days)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
N/A
(10 mo.
study)
Tissue BCFb BAFb
(Concentration ) (L/kg) (L/kg)
Wholebody 31,800
(10.5 ug/g)
Wholebody 11,800
(4.6 ug/g)
Wholebody 3864
(1.275 ug/g)
Wholebody 1038
(0.405 ug/g)
Whole 8667
(2.860 ug/g)
Whole 628
(0.245 ug/g)
Whole 5636
(1.860 ug/g)
Whole 2000
(0.780 ug/g)
Reference
Mason et
al. 2000
Mason et
al. 2000
Mason et
al. 2000
Mason et
al. 2000
a Measured concentration of selenium.
b Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured concentrations of selenium in
water and in tissue (dry weight).
c Estimated from graph.
d Calculated by dividing the reported equilibrium concentration in tissue (steady-state body burden) by the average measured
concentration in water.
e Laboratory food chain: water-> algae -> daphnia -> bluegill.
f Not speciated.
g N/A not applicable.
C-10
Draft November 12, 2004
-------
APPENDIX D
ENVIRONMENTAL FACTORS AFFECTING
SELENIUM TOXICITY AND BIOACCUMULATION
D-1 Draft November 12, 2004
-------
Environmental Factors Affecting Selenium Toxicity and Bioaccumulation
A variety of environmental factors have been shown to influence the toxicity/bioaccumulation of selenium.
A brief summary of the influence of sulfate, hardness, heavy metals, pH, temperature and day length on
selenium toxicity/bioaccumulation is presented below.
Sulfate
In acute toxicity tests and uptake experiments with selenium, sulfate has been shown to antagonize Se
toxicity and Se uptake in plants and animals, frequently with a major effect on Se action. Where multiple
Se forms are used in joint action experiments, Se(VI) is antagonized most by SQ with Se(IV) and Se(II)
affected to a lesser extent. Sulfate has reduced Se mortality responses by 90 percent and Se uptake to 10
percent of controls or less. Thus, sulfate is a major co-factor in a number of Se toxicity and Se uptake
experiments.
In four acute toxicity tests, sulfate antagonized selenate toxicity in three algae species and the cladoceran
Daphnia. The LC50 values of two desmids (Cosmerium spp.) exposed to selenate plus sulfate were 4x and
Sxthe LC50 values of selenate only (Sarma and Jayaraman 1984). The growth ofSelenastrum
capricornutum increased by 50 percent when 11 or 107 (ig/L Se(VI) were combined with 3.3or 33 (ig/L
sulfate (Williams et al. 1994). The toxicity of 490 (ig/L selenate toZ). magna was reduced by 90 percent
mortality by combining it with either 10 or 308 mg/L sulfate. Uptake studies, with one exception,
document sulfate as antagonistic to uptake of selenium. In many cases, Se uptake rates are reduced to 40
to 50 percent of controls (Se alone or lowest SO4 concentration), but there are examples of sulfate reducing
uptake to 20 percent of controls. These examples include a rooted plant (six percent of control rate), an
alga (7 percent), Daphnia (20 percent) and a midge (20 percent).
Of the two algal species mvestigated,Chlamydomonas reinhardtii responded less to sulfate and Se(VI) co-
exposure (Williams et al. 1994) thanSelenastmm capricornutum (7 percent low SO4 rate) (Riedel and
Sanders 1996). Widgeon grass (Ruppia moritima) uptake reductions (Se uptake, high or low sulfate)
occurred most for Se(VI) (6 percent), then Se(IV) (44 percent) and Se(II) (56 percent) (Bailey et al. 1995).
D-2 DraftNovemberl2,2004
-------
Experiments withDaphnia show no interaction of Se and SO4 in a microcosm experiment (Besser et al.
1989). However, other experiments with Se and SO4 show a 43 percent reduction of Se uptake by sulfate
(Hansen et al. 1993) and uptake reductions ranging from 20 to 65 percent among three Se(VI) exposures
and two sulfate levels (Ogle and Knight 1996). Se uptake by a midge,Chironomus decorus, was reduced
to 20 to 65 percent of controls in a 48 hour exposure to 6 mg/L Se(VI) and 3 levels of SO4 (Hansen et al.
1993).
Hardness
Acute toxicity tests of selenium forms with hardness as a variable were conducted with an invertebrate and
three fish species. In all cases, water hardness variations did not cause major changes in the acute toxicity
of selenium. LQ0 value differences due to hardness were no less than half or more than double the LQ0 of
the standard of comparison.
D. magna were exposed to three forms of selenium and one Se mixture in acute toxicity tests (48h LQ0) to
determine the effect of soft (46 mg/L CaCQ) and hard (134 mg/L CaCO3) water on selenium toxicity.
Water hardness did not affect the toxicity of Se(VI) and Se(II), but Se(IV) was slightly more toxic in hard
than soft water (LC50, hard/soft = 0.5), as was the 1:1 mixture of Se(IV) and Se(VI) (LC50, hard/soft = 0.6)
(Ingersoll et al. 1990). Mytilus edulis were exposed to selenite in sea water with salinities of 15, 20, 27
and 30%o (27%o was close to the mussel's natural habitat). Se(IV) influx measured during 2 hours of
exposure demonstrated an effect on uptake as follows: maximum influx at 20%o ; greatest influx difference
= 0.7 max (34%o ) (Wang et al. 1996a).
Fry of chinook salmon and coho salmon were exposed for 96 hr to selenate, selenite and a 1:1 mixture in
soft (42 mg/L CaCO3) and hard (211 mg/L CaCO3) water. Advanced fry of chinook salmon were exposed
to Se(II) in brackish water (333 mg/L CaCO3). In all cases, variable hardness had no effect on the toxicity
of three forms of selenium or the mixture (Hamilton and Buhl 1990b).
Young striped bass (Morone saxatilis) exhibited some differential susceptibility to selenite in hard (285
mg/L CaCO3) vs. soft (40 mg/L CaCO3) water (LC50 hard/soft = 1.8) with Se(IV) in soft water being more
toxic. The LC50 of Se(IV) in 1%0 saline (455 mg/L CaCQ, was not significantly different than Se in soft or
hard water (Palawski et al. 1985).
D-3 DraftNovember 12,2004
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The Se BCF values for young salmon (pnchorhynchus tsawytschd) exposed for 90 days to a Se(VI):Se(IV)
mixture (6:1) were no different in fresh water (371 mg/L CaCQ) or well water (612 mg/L CaCO3).
Exposure for 60 days to Se in l%o saline reduced the Se BCF to approximately 50% of BCFs for well
water and fresh water (Hamilton and Wiedmeyer 1990).
Heavy Metals
Joint action studies with selenium and metals were conducted with cadmium and mercury, which have been
investigated frequently in this regard, and arsenic and molybdenum. The latter two chemicals were
investigated in a chronic test (at least 3 broods) with Ceriodaphnia dubia at exposure concentrations of the
three chemicals that alone caused chronic mortality and reproductive effects. A§5 or Mo+6, combined with
Se(VI) in a chronic test, reduced reproduction and increased cumulative mortality (Naddy et al. 1995).
Mercury uptake experiments with selenite had opposite results in two separate studies with the marine
mussel,Mytilus edulis. In 30 - 50-day tests, Se(IV) uptake was doubled (Se alone = 0.8 ng/g/d) by joint
exposure to Se (30 (ig/L) and HgCl2 (5 (ig/L) (Pelletier 1986a). Uptake of Se in a 96-hr study (Se(IV), 2
(ig/L; HgCl2, 0.1- 1.0 mg/L) decreased as a function of Hg concentration (r2 = - 0.93) (Micallef and Tyler
1987).
The toxicity of Se(IV) and Se(VI) to a fresh water snail (Lymnaea) was reduced by 55 to 66 percent
mortality by 0.1 mg/L cadmium in an 11-day water exposure. Using growth to evaluate toxicity of
selenium-cadmium pairs in two species of marine phytoplankton^rypthecodinium sp., Procentrum sp.),
Prevot and Sayer-Gobillard (1986) demonstrated in both species that the toxicity of the higher Se doses
was reduced by cadmium. Cadmium slightly elevated Se(IV) uptake in gill tissues oCarcinas maenas
(marine shore crabs) but Se levels in two other tissues and carapace were no different than Se exposure in a
29-day experiment.
In summary, cadmium mortality effects were consistent in antagonizing the toxicity of selenium, although
the level of antagonism was low to moderate in these two cases. Mercury effects on Se uptake byMytilus
were not in agreement, i.e. in a 96-hour study, selenium uptake decreased as mercury increased, but in 30 -
50-day tests, mercury enhanced selenium uptake. Both metals are generally toxic which complicates Se-
D-4 DraftNovemberl2,2004
-------
metal investigations. For example, Se interaction with arsenic or molybdenum were conducted with metal
concentrations that were toxic.
pH, Temperature and Day Length
Except for Se(IV) at acidic pH, pH changes in the range associated with natural waters do not have an
appreciable effect on uptake of selenium. Temperature is a major modifying influence on the interaction of
chemicals and aquatic organisms as shown by sediment storage andParamecium experiments. Interaction
by low temperature and day length dramatically enhanced the toxicity of Se in fish chronically exposed
under laboratory conditions.
As presented in the chronic section, Lemly (1993b) investigated the effect of temperature and day-length
effects with selenium on juvenile bluegills exposed for 180 days. Selenium exposures included 4.8 (ig/L in
water (SeVI: SelV =1:1) and Se(II) in food (5.1 (ig/g) and simulation of summer conditions and winter
conditions. Functions monitored during the study were percent lipid content offish (energy reserve),
cumulative mortality, body condition factor, Q)2 and gill pathology and blood abnormalities. All of these
major functions were significantly affected by winter simulation plus selenium in experiments designed to
chronically expose bluegills to a combination of selenium and environmental factors that would reflect
actual exposure of natural fish populations to selenium during seasonal change.
D-5 DraftNovemberl2,2004
-------
APPENDIX E
SITE-SPECIFIC CONSIDERATIONS
E-l DraftNovemberl2,2004
-------
Site-specific Considerations
Aquatic organism uptake of selenium by both water column exposure and dietary pathways has prompted a
number of researchers to investigate the toxicity of selenium under site-specific conditions. Previous site-
specific studies have addressed the water-based chronic criterion of 5 (ig/L through examination of
environmental variables that could potentially influence the availability and/or accumulation of selenium
within the aquatic ecosystem under consideration, thereby either increasing or decreasing the toxic impact
of selenium on the aquatic community (Adams et al. 1998; Canton and VanDerveer 1997; VanDerveer and
Canton 1997).
Now that the recommended chronic criterion is tissue-based, site-specific factors that affect the
bioaccumulation of selenium are not relevant in the modification of the criterion. Recent studies on the
effects of selenium on bluegill in streams receiving wastewater from a coal ash effluent suggest fish
exposed to Se-laden effluents may exhibit tolerance (Lohner et al. 2001a,b,c). The authors found the
bluegill population receiving the coal ash effluent to have an age class structure and condition indices
similar to reference locations despite having selenium concentration in the ovary and whole-body tissues
twice the level of the FCV. Hematological and biochemical assays using samples from exposed bluegill
have shown a reduced response relative to reference fish,but the authors contend that they are not always
related to selenium. The authors hypothesize that selenium speciation, metabolism, bioavailability and
antagonism are possible reasons for the decreased sensitivity of the resident bluegill population in the ash
stream. To date, no experiments on the success on embryo-larval development have been conducted.
In an effort to determine if a proposed multiple-use water development project (Animas La Plata) would
adversely affect aquatic biota in Colorado and New Mexico, Lemly (1997c) conducted a hazard assessment
of selenium using the Protocol Method (Lemly 1995). Using existing environmental monitoring data, the
hazard assessment indicated that selenium poses a siginificant toxic threat to aquatic biota in the Animas
La Plata Project. Incorporating this information into the proposed water development will substantially
reduce the chances of experiencing significant environmental problems similar to those encountered at
Belews Lake and Kesterson National Wildlife Refuge. Once an aquatic system is impacted with selenium,
it could take several to many years before the biological health of the system can be returned to the original
condition prior to perturbation. The Grassland Water District in central California is an example of an
E-2 DraftNovember 12,2004
-------
aquatic system that was contaminated with selenium as a result of subsurface agricultural drainwater used
for wetland management since 1954 (Paveglio et al. 1997). Selenium contamination of aquatic bird food
chains prompted the California State Water Resources Board to mandate the Grassland Water District to
reduce selenium concentration starting in 1985 by essentially filling the wetlands with freshwater only.
Selenium concentrations in a number of aquatic birds have gradually declined since 1985 (1985 to 1994),
but selenium concentrations in some wintering birds still were above concentrations associated with
impaired reproduction in laboratory and field studies. The authors estimated under the current management
strategy, an additional 1 to 13 years from 1994 are needed for selected species to reach background
selenium levels in liver. Thus, approximately 10 to 20 years are needed at this site to reduce the elevated
levels of selenium in avian species and restore normal reproductive success.
E-3 DraftNovemberl2,2004
-------
APPENDIX F
OTHER DATA
F-l Draft November 12, 2004
-------
Other Data
Selenite
Additional data on the lethal and sublethal effects of selenium on aquatic species are presented in Table F-
1. Bringmann and Kuhn (1959a,b, 1976, 1977a, 1979, 1980b, 1981), Jakubczak et al. (1981), and Patrick
et al. (1975) reported the concentrations of selenite that caused incipient inhibition (defined variously, such
as the concentration resulting in a 3% reduction in growth) for algae, bacteria, and protozoans (Table F-l).
Although incipient inhibition might be statistically significant, its ecological importance is unknown.
Albertano and Pinto (1986) found the growth of three red algal species was inhibited at selenite
concentrations that ranged from 790 to 3,9580g/L.
Selenate
Dunbar et al. (1983) exposed fedZ). magna to selenate for seven days and obtained an LQ0 of 1,870 Og/L.
This value is in the range of the 48-hr EQ0s in Table F-l.
Watenpaugh and Beitinger (1985a) found that fathead minnows did not avoid 1 l,20GDg/L selenate during
30-minute exposures (Table F-l). These authors also reported (1985b) a 24-hr LQ0 of 82,000 Og/L for
the same species and they found (1985c) that the thermal tolerance of the species was reduced by 22,200
Og/L. Westerman and Birge (1978) exposed channel catfish embryos and newly hatched fry for 8.5 to 9
days to an unspecified concentration of selenate. Albinism was observed in 12.1 to 36.9% of the fry during
the five years of such exposures. Pyron and Beitinger (1989) also investigated fathead minnows, and after
a 24-hr exposure, no effect on reproductive behavior was found at 36,OOOOg/L, but when adults were
exposed to 20,000 Og/L selenate for 24-hr, edema was observed for their larvae.
The respiratory rate of the eastern oyster, Crassostrea virginica, was unaffected by exposure to selenate at
400 Og/L for 14 days (Fowler et al. 1981). Embryos of the striped bass were quite tolerant to selenate in
dilute salt water (Klauda 1985a, b). There was a 93% successful hatch of embryos at 200,OOOOg/L, but
50% of 72-day-old juveniles died after four days at 87,OOOOg/L. Exposure of juvenile fish for up to 65
days to concentrations of selenate between 39 and l,3600g/L caused developmental anomalies and
pathological lesions.
F-2 Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms
Species
Green alga,
Scenedesmus
quadricauda
Green alga,
Selenastrum
capricornutum
Green alga,
Selenastrum
capricornutum
Green alga,
Selenastrum
capricornutum
Alga,
Chrysochromulina
breviturrita
Red alga,
Cyanidium
caldarium
Red alga,
Cyanidioschyzon
merolae
Red alga,
Galdieria
sulphuraria
Algae (diatoms),
Mixed population
Bacterium,
Escherichia coli
Bacterium,
Pseudomonus putida
Protozoan,
Entosiphon sulcatum
Protozoan,
Microreqma
heterostoma
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acid
Selenious
acid
Selenious
acid
Selenious
acid
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Hardness
(mg/L as
CaCO,) Duration
FRESHWATER
Selenium
96hr
72hr
72 hr
72 hr
30 days
20 days
20 days
20 days
18 days
-
16hr
72 hr
28 hr
Effect
SPECIES
(IV)
Incipient
inhibition (river
water)
Decreased dry
weight and
chlorophyll a
BCF = 12-21b
BCF=11,164C
Increased growth
Inhibited growth
Inhibited growth
Inhibited growth
Inhibited growth
Incipient
inhibition
Incipient
inhibition
Incipient
inhibition
Incipient
inhibition
Concentration1 Reference
2,500 Bringmann and
Kuhn 1959a,b
75 Foe and Knight,
Manuscript
10-100 Foe and Knight,
Manuscript
150 Foe and Knight,
Manuscript
320 Wehr and Brown
1985
3,958 Albertano and
Pinto 1986
3,140 Albertano and
Pinto 1986
790 Albertano and
Pinto 1986
11,000 Patrick et al.
1975
90,000 Bringmann and
Kuhn 1959a
1 1 ,400 Bringmann and
(11,200) Kuhn 1976;
1977a; 1979;
1980b
1.8 Bringmann 1978;
(1.9) Bringmann and
Kuhn 1979;
1980b; 1981
183,000 Bringmann and
Kuhn 1959b
F-3
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Chemical CaCO,) Duration
Effect
Concentration3
Reference
Protozoan,
Chilomonas
paramecium
Protozoan,
Uronema parduezi
Snail,
Lymnaea stagnalis
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Cladoceran
(5th instar),
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran
(preadult),
Daphnia pulex
Ostracod,
Cyclocypris sp.
Amphipod,
Hyalella azteca
Amphipod
(2 mm length),
Hyalella azteca
Amphipod
(2 mm length),
Hyalella azteca
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenious
acid
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
48 hr
20 hr
7.5 days
48 hr
214 24 hr
214 24 hr
329 48 hi
96 hr
14 days
48 hr
21 days
48 hr
220d 48 hr
42 24 hr
100.8 48 hr
329 14 days
133 48 hr
133 10 days
Incipient
inhibition
Incipient
inhibition
LT50
EC50 (river
water)
LC50
EC50
(swimming)
EC50 (fed)
EC50 (fed)
LC50 (fed)
LC50 (fed)
Did not reduce
oxygen
consumption or
filtering rate
LC50
LC50 (fed)
LC50
LC50
(fed)
62
118
3,000
2,500
16,000
9.9
710
430
430
685
160
680
1,200
>498
130,000
70
623
312
Bringmann and
Kuhn 1981;
Bringmann et al.
1980
Bringmann and
Kuhnl980a;
1981
Van Puymbroeck
etal. 1982
Bringmann and
Kuhn 1959a,b
Bringmann and
Kuhn 1977a
Bringmann and
Kuhn 1977b
Halter etal. 1980
Adams and
Heidolphl985
Johnston 1987
Kimball,
Manuscript
Reading and
Buikemal980
Owsley 1984
Halter etal. 1980
Brasher and Ogle
1993
Brasher and Ogle
1993
F-4
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Chemical CaCO,) Duration
Effect
Concentration3 Reference
Amphipod
(2 mm length),
Hyalella azteca
Midge (first instar),
Chironomus riparius
Midge (first instar),
Chironomus riparius
Coho salmon (fry),
Oncorhynchus
kisutch
Rainbow trout (fry),
Oncorhynchus
mykiss
Rainbow trout (fry),
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
133 24 days
134 48 h
40-48 48 h
325 43 days
334 21 days
334 21 days
330 5 days
325 48 days
325 96 days
4wk
4wk
4wk
42 wk
LOEC
reproduction
(static-renewal)
LC50
LC50
LC50
LC50
Reduced growth
LC50
LC50
LC50
MATC
survival
MATC
survival
BCF = 23
MATC growth
(dietary only
exposure)
200
7,950
14,600
160
460
250
2,700
2,750
500
280
200
4.7
Hg/g dw
(whole-body)
100
>9.96
Hg Se/g dw
(food)
Brasher and Og
1993
Ingersoll et al.
1990
Ingersoll et al.
1990
Adams 1976
Adams 1976
Adams 1976
Adams 1976
Adams 1976
Adams 1976
Gissel-Nielsen
and Gissel-
Nielsen 1978
Gissel-Nielsen
and Gissel-
Nielsen 1978
Gissel-Nielsen
and Gissel-
Nielsen 1978
Goettl and
Davies 1978
F-5
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Chemical CaCO,) Duration
Effect
Concentration3
Reference
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout
(fertilized egg),
Oncorhynchus
mykiss
Rainbow trout
(embryo),
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout
(sac fry),
Oncorhynchus
mykiss
Rainbow trout
(sac fry),
Oncorhynchus
mykiss
Rainbow trout
(egg ),
Oncorhynchus
mykiss
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
42 wk
135 9 days
135 96 hr
9 days
135 96 hr
9 days
135 41 days
135 50 wk
135 44 wk
120 hr
90 days
272 90 days
272 90 days
96 hr
MATC survival
(dietary only
exposure)
LC50
LC50
(fed)
LC50
(fed)
LOAEC
(Reduced hatch
of eyed embryos)
Decreased iron
in blood and red
cell volume
BCF = 33.2
BCF = 21.1
Did not reduce
survival or time
to hatch
Chronic value for
survival
LC50
MATC
survival
BCF = 17.5
BCF = 3.5
5.34
Hg Se/g dw
(food)
7,020
7,200
5,410
8,200
6,920
26
53
53
10,000
14
55.2e
31.48
0.4
45.6
Goettl and
Davies 1978
Hodson et al.
1980
Hodson et al.
1980
Hodson et al.
1980
Hodson et al.
1980
Hodson et al.
1980
Hodson et al.
1980
Klaverkamp et
al. 1983b
Mayer et al.
1986
Hunnetal. 1987
Hunnetal. 1987
Hodson et al.
1986
F-6
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Species
Hardness
(mg/L as
Chemical CaCO,) Duration
Effect
Concentration3 Reference
Rainbow trout
(embryo),
Oncorhynchus
mykiss
Rainbow trout
(sac-fry),
Oncorhynchus
mykiss
Rainbow trout
(swim-up fry)
Oncorhynchus
mykiss
Northern pike,
Esox lucius
Goldfish,
Carassius auratus
Goldfish,
Carassius auratus
Goldfish,
Carassius auratus
Goldfish,
Carassius auratus
Goldfish,
Carassius auratus
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Creek chub,
Semotilus
atromaculatus
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Selenium
dioxide
Sodium
selenite
Sodium
selenite
Selenium
dioxide
Selenium
dioxide
Selenium
dioxide
Sodium
selenite
Sodium
selenite
Selenious
acid
Selenium
dioxide
96 hr
96 hr
96 hr
10.2 76 hr
157 14 days
10 days
46 days
7 days
48 hr
157 9 days
329 96 hr
329 14 days
220d 8 days
48 hr
BCF = 3.1
BCF = 3.0
BCF=13.1
BCF= 1.6
BCF = 80.3
BCF = 20.2
LC50
LC50
Mortality
Gradual anorexia
and mortality
LC50
Conditional
avoidance
LC50
LC50
(fed)
LC50
(fed)
LC50
(fed)
Mortality
0.4
45.6
0.4
45.6
0.4
45.6
11,100
6,300
5,000
2,000
12,000
250
2,100
1,000
600
420
* 12,000
Hodson et al.
1986
Hodson et al.
1986
Hodson et al.
1986
Klaverkamp et
al. 1983a
Card well et al.
1976a,b
Ellis 1937; Ellis
etal. 1937
Ellis etal. 1937
Weir and Hine
1970
Weir and Hine
1970
Card well et al.
1976a,b
Halter etal. 1980
Halter etal. 1980
Kimball,
Manuscript
Kim etal. 1977
F-7
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Species
Bluegill,
Lepomis
macrochirus
Bluegill,
Lepomis
macrochirus
Bluegill (juvenile),
Lepomis
macrochirus
Bluegill (juvenile),
Lepomis
macrochirus
Largemouth bass
(juvenile),
Micropterus
salmoides
Yellow perch,
Percaflavescens
African clawed frog,
Xenopus laevis
African clawed frog,
Xenopus laevis
Alga,
Chrysochromulina
breviturrita
Snail,
Lymnaea stagnalis
Cladoceran,
Daphnia magna
Cladoceran
(juvenile),
Daphnia magna
Cladoceran
(5th instar),
Daphnia magna
Chemical
Sodium
selenite
Selenium
dioxide
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenite
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
CaCO,) Duration
318 48 days
157 14 days
16 323 days
25 120 days
and
200
25 120 days
and
200
10.2 10 days
7 days
1-7 days
Selenium
30 days
6 days
129.5 7 days
48 hr
48 hr
Effect
LC50
LC50
MATC larval
survival
(dietary only
exposure)
No mortality
No mortality
LC50
LC50
Cellular damage
(VI)
Increased
growth
LT50
LC50
(fed)
LC50
(fed)
LC50
(fed)
Concentration3
400
12,500
19.75
Hg Se/g dw
(food)
>10
10
4,800
1,520
2,000
50
15,000
1,870
550
750
Reference
Adams 1976
Card well et al.
1976a,b
Woock et al.
1987
Lemly 1982
Lemly 1982
Klaverkamp et
al. 1983a,b
Browne and
Dumont 1980
Browne and
Dumont 1980
Wehr and Brown
1985
Van Puymbroeck
etal. 1982
Dunbar et al.
1983
Johnston 1987
Johnston 1987
F-8
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Chemical CaCO,) Duration
Effect
Concentration3 Reference
Cladoceran
(5th instar),
Daphnia magna
Amphipod
(2 mm length),
Hyalella azteca
Amphipod
(2 mm length),
Hyalella azteca
Amphipod
(2 mm length),
Hyalella azteca
Midge (first instar),
Chironomus riparius
Midge (first instar),
Chironomus riparius
Rainbow trout
(embryo, larva),
Oncorhynchus
mykiss
Goldfish
(embryo, larva),
Carrassius auratus
Goldfish,
Carassius auratus
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
~
90 hr
133 48 hr
133 10 days
133 24 days
134 48 h
40-48 48 h
104 28 days
(92-110)
195 7 days
24 hr
337.9 48 days
338 48 days
51 30min
24 hr
42% of organ-
isms had visible
changes in gut
morphology
LC50
LC50
(fed)
LOEC
reproduction
(static renewal)
LC50
LC50
EC50 (death and
deformity)
EC50 (death and
deformity)
BCF=1.42
BCF= 1.15
BCF=1.47
BCF = 0.88
BCF=1.54
LC50
LC50
No avoidance
LC50
250
2378
627
>700
16,200
10,500
5,000
(4,180)
(5,170)
8,780
0.45
0.9
1.35
2.25
4.5
2,000
1,100
11,200
82,000
Johnston 1989
Brasher and Ogle
1993
Brasher and Ogle
1993
Brasher and Ogle
1993
Ingersoll et al.
1990
Ingersoll et al.
1990
Birge 1978;
Birge and Black
1977; Birge et al.
1980
Birge 1978
Sharma and
Davis 1980
Adams 1976
Adams 1976
Watenpaugh and
Beitinger 1985a
Watenpaugh and
Beitinger 1985b
F-9
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Chemical CaCCO
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Channel catfish
(embryo, fry),
Ictalurus punctatus
Narrow-mouthed
toad
(embryo, larva),
Gastrophryne
carolinensis
Bluegill (juvenile),
Lepomis
macrochirus
Bluegill (juvenile),
Lepomis
macrochirus
Bluegill
(2 yr and adult),
Lepomis
macrochirus
Bluegill
(2 yr and adult),
Lepomis
macrochirus
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Seleno-L-
methionine
Seleno-L-
methionine
Selenium
Selenium
44-49
160-180
160-180
90
195
16
283
Duration
24 hr
7 days
24 hr
24 hr
8.5-9
days
7 days
Effect
Reduced thermal
tolerance
Chronic value -
growth
Chronic value-
growth
Chronic value-
survival
No effect on
reproductive
behavior
Edema in larvae
produced from
adults exposed to
Selenium VI
Induced albinism
EC50 (death and
deformity)
Concentration3
22,200
1,739
561
2,000
36,000
20,000
_
90
Reference
Watenpaugh and
Beitinger 1985c
Norberg-King
1989
Pyron and
Beitinger 1989
Pyron and
Beitinger 1989
Westerman and
Birgel978
Birge 1978;
Birge and Black
1977; Birge et al.
1979a
Organo-selenium
323 days
90 days
field
field
MATC larval
survival
(dietary only
exposure)
EC20 survival
(dietary only
exposure)
NOEC
deformities
NOEC
deformities
20.83
Hg Se/g dw
(food)
>13.4
Hg/g dw
(food)
53.83
jig Se/g dw
(liver)
23.38
jig Se/g dw
(ovaries)
Woock et al.
1987
Cleveland et al.
1993
Reashetal. 1999
Reashetal. 1999
F-10
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Hardness
(mg/L as
Species
Redear sunfish
(adult),
Lepomis
microlophus
Chemical
Selenium
CaCO,) Duration
field
Effect
LOEC Adverse
histopathological
alterations
Concentration3
<38.15
Hg Se/g dw
Reference
Sorensenl988
Selenium Mixtures
Phytoplankton,
Mixed population
Cladoceran
(<24 hr),
Daphnia magna
Cladoceran
(<24 hr),
Daphnia magna
Midge (<24-hr),
Chironomus riparius
Bluegill (juvenile),
Lepomis
macrochirus
Bluegill (juvenile),
Lepomis
macrochirus
Species
Anaerobic
bacterium,
Methanococcus
vannielli
Bacterium,
Vibrio fisheri
Green alga,
Chlorella sp.
Selenium
Selenite-
Selenate
mixture
Selenite-
Selenate
mixture
Selenite-
Selenate
mixture
Selenite-
Selenate
mixture
Selenite-
Selenate
mixture
Chemical
Sodium
selenite
Sodium
selenite
Sodium
selenite
field
138 21 days
138 21 days
138 30 days
283 60 days
283 60 days
Salinity
(g/kg) Duration
SALTWATER
Selenium
HOhr
5 min
32 14 days
Reduced growth
rates
MATC
growth
MATC
productivity
MATC
emergence
NOEC survival
EC20 survival
Effect
SPECIES
(IV)
Stimulated growth
50% decrease in
light output
(Micro tox®)
5-12% increase in
growth
18
115.2
HgSe/L
21.590g/gdw
(whole-body)
503.6
340
4.07
Hg/g dw
(whole body)
Concentration
(ug/L)a
79.01
68,420
10-10,000
Riedel et al.
1991
Ingersoll et al.
1990
Ingersoll et al.
1990
Ingersoll et al.
1990
Cleveland et al.
1993
Cleveland et al.
1993
Reference
Jones and
Stadtman
1977
Yu et al.
1997
Wheeler et
al. 1982
F-ll
Draft November 12, 2004
-------
Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Species
Green alga,
Platymonas
subcordiformis
Green alga,
Dunaliella
primolecta
Diatom,
Skeletonema
costatum
Diatom,
Chaetoceros
muelleri
Diatom,
Phaeodactylum
tricornutum
Diatom,
Thallassiosira
aestivalis
Brown alga,
Fucus spiralis
Red alga,
Porphyridium
cruentum
Bacterium,
Vibrio fisheri
Green alga,
Chlorella sp.
Green alga,
Chlorella sp.
Green alga,
Dunaliella
primolecta
Green alga,
Dunaliella
primolecta
Green alga,
Dunaliella
primolecta
Chemical
Sodium
selenite
Sodium
selenite
Selenium
dioxide
Selenium
dioxide
Selenium
dioxide
Selenium
oxide
Sodium
selenite
Sodium
selenite
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Salinity
(g/kg) Duration
32 14 days
32 20 days
5 days
6 days
8 days
29-30 72 hr
60 days
32 27 days
Selenium
1 5 min
32 14 days
32 4-5 days
32 14 days
32 14 days
32 4-5 days
Effect
23% increase in
growth
Increased growth;
induced glutathione
peroxidase
BCF= 18,000
BCF = 16,000
BCF = 10,000
BCF = 337,000
BCF = 65,000
BCF = 5,000
BCF = 109,000
BCF = 27,000
BCF = 7,000
No effect on cell
morphology
1355% increase in
growth of thalli
Increase growth;
induced glutathione
peroxidase
(VI)
50% decrease in
light output
(Micro tox®)
No effect on rate of
cell
100% mortality
No effect on rate of
cell population
growth
71% reduction in
rate of cell
population growth
100% mortality
Concentration
(ug/L)a
100-10,000
4,600
0.06
0.79
3.6
0.06
0.79
3.6
0.06
0.79
3.6
78.96
2.605
4,600
3,129,288
10-1,000
10,000
10-100
1,000
10,000
Reference
Wheeler et
al. 1982
Gennity et al.
1985a,b
Zhang et al.
1990
Zhang et al.
1990
Zhang et al.
1990
Thomas et al.
1980a
Fries 1982
Gennity et al.
1985a,b
Yu et al.
1997
Wheeler et
al. 1982
Wheeler et
al. 1982
Wheeler et
al. 1982
Wheeler et
al. 1982
Wheeler et
al. 1982
F-12
Draft November 12, 2004
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Table F-l. Other Data on Effects of Selenium on Aquatic Organisms (continued)
Species
Green alga,
Platymonas
subcordiformis
Green alga,
Platymonas
subcordiformis
Green alga,
Platymonas
subcordiformis
Green alga,
Platymonas
subcordiformis
Brown alga,
Fucus spiralis
Red alga,
Porphridium
cruentum
Red alga,
Porphyridium
cruentum
Eastern oyster
(adult),
Crassostrea
virginica
Striped bass
(embryo),
Morone saxatilis
Striped bass
(larva),
Morone saxatilis
Striped bass
(juvenile),
Morone saxatilis
Striped bass
(juvenile),
Morone saxatilis
Chemical
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Sodium
selenate
Salinity
(g/kg) Duration
32 14 days
32 14 days
32 14 days
32 4-5 days
60 days
32 14 days
32 4-5 days
34 14 days
7.2-7.5 4 days
4.0-5.0 4 days
3.5-5.5 9-65 days
3.5-5.5 45 days
Concentration
Effect (ug/L)a
No effect on rate of 10
cell population
growth
16% decrease in 100
rate of cell
population growth
50% decrease in 1,000
rate of cell
population growth
100% mortality 10,000
160% increase in 2.605
growth rate of thalli
23-35% reduction 10-1,000
in rate of cell
population growth
100% mortality 10,000
No significant 400
effect on respiration
rate of gill tissue
93% successful 200,000
hatch and survive
LC50 (control 13,020
survival= 77%)
Significant 39-1,360
incidence of
development
anomalies of lower
jaw
Significant 1,290
incidence of severe
blood cytopathology
Reference
Wheeler et
al. 1982
Wheeler et
al. 1982
Wheeler et
al. 1982
Wheeler et
al. 1982
Fries 1982
Wheeler et
al. 1982
Wheeler et
al. 1982
Fowler et al.
1981
Klauda
1985a,b
Klauda
1985a,b
Klauda
1985a,b
Klauda
1985a,b
Concentration of selenium, not the chemical. Units are |ig selenium/L of water unless noted otherwise.
Converted from dry weight to wet weight basis (see Guidelines)
Growth of algae was inhibited
From Smith et al. (1976).
Calculated from the published data using probit analysis and allowing for 8.9% spontaneous mortality.
F-13
Draft November 12, 2004
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Other Data - Endangered Species
Two similar studies were conducted in subsequent years, 1996 and 1997, to determine the effects of site water
and site food contaminated with selenium on the endangered species, razorback sucketfyrauchen texanus
(Hamilton et al. 2001a,b). Both studies show marked effects on the survival of razorback sucker larvae
exposed to contaminated food and to a lesser extent, contaminated water. Although the data convincingly
demonstrate effects to larval survival from exposure to contaminated food, it was not considered acceptable
data for use in the derivation of the chronic criterion because of inconsistencies between levels of selenium in
the food and larvae and degree and time to response. A summary of each of these two studies is presented
below.
Evaluation of Contaminant Impacts on Razorback Sucker held in Flooded Bottomland Sites Near Grand
Junction , Colorado - 1996 (Hamilton et al. 2001a)
This study was initiated with 5-day old razorback sucker larvae spawned from adults which were previously
held (9 months) in three different location along the Colorado River that contained varying levels of selenium:
Horsethief (the designated reference site which receives water pumped directly from the Colorado River near
Fruita, CO), Adobe Creek (low level selenium contamination), and North Pond (high level selenium
contamination). The selenium content in the eggs from three Horsethief females ranged from 5.8 to 6.6 (ig
Se/g dw, and the selenium content in adult muscle plugs at spawning was from 3.4 to 5.0 (ig Se/g dw. The
selenium content in the eggs from three Adobe Creek females ranged from 38.0 to 54.5 (ig Se/g dw, and the
selenium content in adult muscle plugs at spawning was from 11.5 to 12.9 (ig Se/g dw. The selenium content
in the eggs from three North Pond females ranged from 34.3 to 37.2 (ig Se/g dw, and the selenium content in
adult muscle plugs at spawning was from 14.1 to 17.3 (ig Se/g dw. The selenium content in the eggs from a
hatchery brood stock female was 7.1 (ig Se/g dw, and the selenium content in adult muscle plugs at spawning
ranged from 2.6 to 13.8 (ig Se/g dw. The razorback sucker larvae spawned from fish hatchery brood stock
and held in Colorado River (Horsethief) water were used as an additional reference group of test fish.
The experimental groups were subdivided into those receiving reference water (hatchery water; 24-Road Fish
Hatchery) or site water. They were further subdivided into those receiving a daily ration of reference food
(brine shrimp) or zooplankton collected from each site where their parents were exposed for the previous 9
months. A total of 60 larvae from each of the four adult sources (Horsethief, Adobe Creek, North Pond,
F-14 Draft November 12, 2004
-------
Brood Stock) were exposed to each treatment (2 replicates x 3 spawns x 10 fish/beaker). The larvae were held
in beakers containing 800 mis of test water. Fifty percent of the test water was renewed daily.
Treatment conditions during the 30-day larval study:
Source of Larvae
Horsethief Adults
Adobe Creek Adults
North Pond Adults
Hatchery raised Adults
Treatments
Reference food: Reference water
Reference food: Site water
Site food: Reference water
Site food: Site water
Reference food: Reference water
Reference food: Site water
Site food: Reference water
Site food: Site water
Reference food: Reference water
Reference food: Site water
Site food: Reference water
Site food: Site water
Reference food: Reference water
Reference food: Site water
Site food: Reference water
Site food: Site water
Sein
food
(jig/g dw)
2.7
2.7
5.6
5.6
2.7
2.7
20
20
2.7
2.7
39
39
2.7
2.7
5.6
5.6
Sein
water
(Mg/L)
<1
0.9
<1
0.9
<1
5.5
<1
5.5
<1
10.7
<1
10.7
<1
0.9
<1
0.9
Growth, survival and development were evaluated amongst treatment groups for up to 30 days in the treatment
conditions. Each treatment group was fed once daily after renewal. Test waters were collected every day
from each site as grab samples for the renewal. A small portion of this water was retained at 3- and 7-day
intervals for an analysis of total and dissolved selenium concentrations. At approximately 2-day intervals,
aquatic invertebrates and brine shrimp not used for feeding were sieved from the media for selenium analysis.
The number of live fish were recorded daily. After the 30-day exposure period, the surviving fish were
F-15
Draft November 12, 2004
-------
sacrificed and measured for total length. At this same time, approximately four fish from each treatment,
when available, were collected as a composite sample and analyzed for selenium. Specific treatment
conditions were as those described above.
After 30 days of exposure in the reference food-reference water treatment, survival of razorback sucker larvae
from brood stock and Horsethief adults (89 and 87 percent, respectively) was slightly higher than those from
Adobe Creek adults (84 percent) and North Pond adults (75 percent). Corresponding selenium concentrations
in larval whole-body tissue were 3.6, 3.3, 7.7 and 9.7 (ig Se/g dw, respectively. Survival was similar or
slightly reduced in larvae from all four sources after 30 days of exposure in the reference food-site water
treatments; corresponding selenium concentrations in larval whole-body tissue were 5.2, 5.1, 12.7 and 15.2 (ig
Se/g dw, respectively. In contrast, none of the larvae spawned from parents from Horsethief, Adobe Creek, or
North Pond survived to 30 days when fed zooplankton collected from the three sites, irrespective of the water
type they were exposed to (i.e., reference or site). Only the larvae from brood stock adults, which were fed
zooplankton from the Horsethief site for this treatment, survived, and even these larvae suffered substantial
mortality (40 and 60 percent respectively). The mean selenium concentrations in whole-body tissue of larvae
from brood stock adults after the 30-day exposures were 5.4 (ig Se/g dw (site food-reference water treatment)
and 6.9 (ig Se/g dw (site food-site water treatment).
Several inconsistencies were observed that suggest selenium may not be solely responsible for the effect on
larval survival. Larval survival in the Adobe Creek treatment group exposed to reference water and reference
food was 84 percent, similar to control survival (86-89 percent). The selenium concentration in the larvae
from this Adobe Creek treatment group after 30 days was highei(7.7 (ig/g dw) than brood stock fish (5.4 (ig
Se/g dw) which had a lower 30-day survival (62 percent). Also, the time to 50 percent mortality between the
site food treatments, where most mortality occurred, was not related to selenium concentration in the diet or in
the larvae.
F-16 Draft November 12, 2004
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Evaluation of Contaminant Impacts on Razorback Sucker held in Flooded Bottomland Sites Near Grand
Junction , Colorado - 1997 (Hamilton etal. 2001b)
In a similar 30-day larval study conducted by the authors thein following year (1997), razorback sucker
larvae from a single hatchery brood stock female (11 (ig Se/g dw muscle) were subjected to one of the sixteen
different combined water and dietary exposure conditions described in the earlier (1996) study. The female
parent was held at Horsethief Canyon State Wildlife Area before spawning. The larvae were held in beakers
containing 800 mis of test water as before, fifty percent of the test water was renewed daily. Specific
treatment conditions for the 1997 30-day larval study were as follows:
Treatment conditions during the 30-day larval study:
Water Treatments
Reference food (brine shrimp):
Reference water (24-Road Hatchery)
Reference food: Site water (Horsethief)
Reference food: Site water (Adobe Creek)
Reference food: Site water (North Pond)
Horsethief food: Reference water
Horsethief food: Site water (Horsethief)
Horsethief food: Site water (Adobe Creek)
Horsethief food: Site water (North Pond)
Adobe Creek food: Reference water
Adobe Creek food: Site water (Horsethief)
Adobe Creek food: Site water (Adobe Creek)
Adobe Creek food: Site water (North Pond)
North Pond food: Reference water
North Pond food: Site water (Horsethief)
North Pond food: Site water (Adobe Creek)
North Pond food: Site water (North Pond)
Se in
food
(jig/g dw)
3.2
6.0
32.4
52.5
3.2
6.0
32.4
52.5
3.2
6.0
32.4
52.5
3.2
6.0
32.4
52.5
Se in
water
(^g/L)
<1
1.6
3.4
13.3
<1
1.6
3.4
13.3
<1
1.6
3.4
13.3
<1
1.6
3.4
13.3
F-17
Draft November 12, 2004
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In this year's study, after 30 days of exposure, there was also good survival of razorback sucker larvae fed
reference food (brine shrimp) and held in reference water or water from Horsethief (83 and 81 percent,
respectively). The survival of these larvae was significantly greater than survival of larvae fed brine shrimp
and held in water from North Pond (only 52 percent). Corresponding selenium concentrations in larval whole-
body tissue after 10 days were 6.3, 6.7, and 11 (ig Se/g dw, respectively. The average concentrations of
selenium in the water for the three treatments were <1, 1.6, and 13.3 (ig Se/L. After 30 days the mean
selenium concentrations in these larvae were 5.2, 5.2, and 16 (ig Se/g dw, respectively. Survival was
markedly reduced (0 to 30 percent survival) in the remainder treatments where larvae were fed zooplankton
from the various sites. Complete mortality was experienced by larvae exposed to Horsethief food and
reference water treatment after 30 days.
Similar to the previous study, there are several inconsistencies in the results that suggested selenium may not
be solely responsible for the effect on larval survival. The most notable inconsistency was that the greatest
effect on larval survival (percent survival or time to 50 percent mortality) was from exposure to Horsethief
food, the food with the lowest selenium contamination.
F-18 Draft November 12, 2004
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APPENDIX G
UNUSED DATA
G-1 Draft November 12, 2004
-------
Unused Data
Based on the requirements set forth in the guidelines (Stephen et al. 1985) the following studies are not
acceptable for the following reasons and are classified as unused data.
Studies Were Conducted with Species That Are Not Resident in North America
Ahsanullah and Brand (1985) Hiraika et al. (1985) Rouleau et al. (1992)
Ahsanullah and Palmer (1980) Juhnke and Ludemann (1978) Sastry and Shukla (1994)
Baker and Davies (1997) Kitamura (1990) Savant and Nilkanth (1991)
Barghigiani et al. (1993) Manoharan and Prabakaran (1994) Shultz and Ito (1979)
Chidambaram and Sastry (1991a,b) Minganti et al. (1994, 1995) Srivastava and Tyagi (1985)
Congiu et al. (1989) Niimi and LaHam (1975, 1976) Takayanagi (2001)
Cuvin and Furness (1988) Regoli (1998) Tomasik et al. (1995b)
Fowler and Benayoun (1976a,b) Regoli and Principato (1995) Tian and Liu (1993)
Gaikwad(1989) Rhodes et al. (1994) Wrench (1978)
Gotsis (1982) Ringdal and Julshamn (1985)
Deelstra et al. (1989), Forsythe and Klaine (1994), Okasako and Siegel (1980) and Petrucci et al. (1995)
conducted tests with brine shrimp species that are too atypical to be used in derving national criteria.
These Reviews Only Contain Data That Have Been Published Elsewhere
Adams and Johnson (1981) Hall and Burton (1982) National Research Council (1976)
Biddinger and Gloss (1984) Hodson and Hilton (1983) Neuhold (1987)
Bowie et al. (1996) Hodson et al. (1984) NCDNR&CD (1986)
Brandaoetal. (1992) Jenkins (1980) Peterson and Nebeker (1992)
Brooks (1984) Kaiser et al. (1997) Phillips and Russo (1978)
Burton and Stemmer (1988) Kay (1984) Presser (1994)
Chapman et al. (1986) LeBlanc (1984) Roux et al. (1996)
Davies (1978) Lemly (1993c, 1996ab, 1997d) Thompson et al. (1972)
Devillers et al. (1988) Lemly and Smith (1987) Versar (1975)
Eisler(1985) McKee and Wolf (1963)
G-2 Draft November 12, 2004
-------
Authors Did Not Specify the Oxidation State of Selenium Used in Study
Greenberg and Kopec (1986) Kramer et al. (1989) Rauscher (1988)
Hutchinson and Stokes (1975) Mahan et al. (1989) Snell et al. (1991b)
Kapu and Schaeffer (1991)
Selenium Was a Component
Apteetal. (1987)
Baeretal. (1995)
Baker et al. (1991)
Bergetal. (1995)
Besseretal. (1989)
Biedlingmaier and Schmidt (1989)
Bjoernberg(1989)
Bjoernberg et al. (1988)
Blockmann et al. (1995)
Boissonetal. (1989)
Bondavalli et al. (1996)
Bowmeretal. (1994)
Briegeretal. (1992)
Burton and Pinkney (1984)
Burton etal. (1983, 1987)
Cherry et al. (1987)
Cieminski and Flake (1995)
Clark etal. (1989)
Cooke and Lee (1993)
Cossuetal. (1997)
Coyle etal. (1993)
Crane etal. (1992)
Crock etal. (1992)
Cushman et al. (1977)
Davies and Russell (1988)
de Peyster et al. (1993)
Dickman and Rygiel (1996)
Dierenfeld et al. (1993)
Drndarski et al. (1990)
Eriksson and Forsberg (1992)
Eriksson and Pedros-Alio (1990)
of an Effluent, Fly Ash, Formulation,
Fairbrotheretal. (1994)
Favaetal. (1985a,b)
Ferocietal. (1997)
Finger and Bulak (1988)
Finley(1985)
Fisher and Wente (1993)
Fjeld and Rognerud (1993)
Fletcher etal. (1994)
Follett(1991)
Gerhardt(1990)
Gerhardt et al. (1991)
Gibbs and Miskiewicz (1995)
Graham etal. (1992)
Gunderson et al. (1997)
Hall (1988)
Hall etal. (1984, 1987, 1988,1992)
Hamilton et al. (1986, 2000)
Harrison et al. (1990)
Hartwell etal. (1987ab, 1988,
1997)
Hatcher etal. (1992)
Haynesetal. (1997)
Haywardetal. (1996)
Hellou etal. (1996)
Henebry and Ross (1989)
Henry et al. (1989, 1990, 1995)
Hildebrand etal. (1976)
Hjeltner and Julshman (1992)
Hockett and Mount (1996)
Hodson(1990)
Hoffman etal. (1988, 1991)
Mixture, Sediment or Sludge
Homziak etal. (1993)
Hopkins et al. (2000)
Hothem and Welsh (1994a)
Jackson(1988)
Jackson etal. (1990)
Jacquezetal. (1987)
Jay and Muncy (1979)
Jayasekera(1994)
Jayasekera and Rossbach (1996)
Jenner andBowmer (1990) (1992)
Jenner and Janssen-Mommen
(1989)
Jin etal. (1997)
Jorgensen and Heisinger (1987)
Karlson and Frankenberger (1990)
Kemble etal. (1994)
Kenned (1986)
Kerstenetal. (1991)
King and Cromartie (1986)
King etal. (1991,1994)
Klusek etal. (1993)
Koh and Harper (1988)
Koike etal. (1993)
Krishnaja etal. (1987)
Kruuk and Conroy (1991)
Kuehl and Haebler (1995)
Kuehl etal. (1994)
Kuss etal. (1995)
Landau etal. (1985)
Livingstone et al. (1991)
Lobel etal. (1990)
Draft November 12, 2004
-------
Luoma and Phillips (1988)
Lundquistetal. (1994)
Lyle(1986)
MacFarlane et al. (1986)
Mann and Fyfe (1988)
Marcogliese et al. (1987)
Marvin etal. (1997)
Maureretal(1999)
McCloskey and Newman (1995)
McCloskey etal. (1995)
McCrea and Fischer (1986)
McLean etal. (1991)
Mehrle etal. (1987)
Metcalf-Smith(1994)
Micallef and Tyler (1989)
Mikac etal. (1985)
Miles and Tome (1997)
Miller etal. (1996)
Misitano and Schiewe (1990)
Moore (1988)
Munawar and Legner (1993)
Muskettetal. (1985)
Naddy etal. (1995)
Nielsen and Bjerregaard (1991)
Norman etal. (1992)
Nuutinen & Kukkonen (1998)
Oberbach and Hartfield (1987,
1988)
Oberbach et al. (1989)
Ohlendorfetal. (1989, 1990, 1991)
Olsen and Welsh (1993)
Peters etal.(1999)
Phillips and Gregory (1980)
Pratt and Bowers (1990)
Presser and Ohlendorf (1987)
Prevot and Sayer-Gobillard (1986)
Pritchard(1997)
Pyleetal. (2001)
Reash et al. (1988, in press)
Rhodes and Burke (1996)
Ribeyre etal. (1995)
Rice etal. (1995)
Riggs and Esch( 1987)
Riggsetal. (1987)
Robertson etal. (1991)
Roper etal. (1997)
Russell etal. (1994)
Rytheretal. (1979)
Saiki and Jenings (1992)
Saiki and Ogle (1995)
Saleh etal. (1988)
Seelye etal. (1982)
Sevareid and Ichikawa (1983)
Skinner (1985)
Somerville et al. (1987)
Sorenson and Bauer (1983)
Specht etal. (1984)
Steele etal. (1992)
Stemmeretal. (1990)
Summers etal. (1995)
Thomas etal. (1980b)
Timothy etal. (2001)
Trieff etal. (1995)
Turgeon and OConner (1991)
Twerdok etal. (1997)
Ursal(1987)
Van Metre and Gray (1992)
Wahl etal. (1994)
Wandan and Zabik (1996)
Wang etal. (1992, 1995)
Welsh (1992)
Weresetal. (1990)
White and Geitner (1996)
Wiemeyeretal. (1986)
Wildhaber and Schmitt (1996)
Williams etal. (1989)
Wolfe etal. (1996)
Wolfenberger(1987)
Wong and Chau (1988)
Wong etal. (1982)
Wu etal. (1997)
Yamaoka etal. (1994)
Zagattoetal. (1987)
Zaidi etal. (1995)
Zhang etal. (1996)
Exposed enzymes, excised tissue or tissue extractor
Tripathi and Pandey (1985) and Heinz (1993b) used test organisms that had been previously exposed to
pollutants in food or water.
Albersetal. (1996)
Al-Sabti (1994, 1995)
Arvy etal. (1995)
Augieretal. (1993)
A very etal. (1996)
Baatrup(1989)
Baatrup and Dansher (1987)
Baatrupetal. (1986)
Babich etal. (1986, 1989)
G-4
Draft November 12, 2004
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Harrington et al. (1997)
Becker etal.(1995a,b)
Belletal. (1984, 1985, 1986a,b,
1987ab)
Berges and Harrison (1995)
Blondinetal. (1988)
Boissonetal. (1996)
Bottinoetal. (1984)
Braddon(1982)
Braddon-Galloway and Balthrop
(1985)
Bradford et al. (1994a,b)
Brandt et al. (1990)
Byletal. (1994)
Chandy and Patel (1985)
Chen etal. (1997)
Cheng etal. (1993)
Christensen and Tucker (1976)
Dabbert and Powell (1993)
DeQuiroga et al. (1989)
Dierickx(1993)
Dietrich etal. (1987)
Dillio etal. (1986)
Doyotteetal. (1997)
Drotaretal. (1987)
Dubois and Callard (1993)
Ebringer etal. (1996)
Engberg and Borsting (1994)
Engbergetal. (1993)
Eunetal. (1993)
Foltinova and Gajdosova (1993)
Foltinova et al. (1994)
Freeman and Sanglang (1977)
Grubor-Lajsic etal. (1995)
Hait and Sinha (1987)
Hanson (1997)
Heisinger and Scott (1985)
Heisinger and Wail (1989)
Henderson et al. (1987)
Henny and Bennett (1990)
Hoffman and Heinz (1988, 1998)
Hoffman et al. (1989, 1998)
Hontelaetal. (1995)
Hoglund(1991)
Hsu etal. (1995)
Hsu and Goetz (1992)
Ishikawa et al. (1987)
James etal. (1993)
Jovanovic etal. (1995, 1997)
Kai etal. (1995)
Kedziroski et al. (1996)
Kelley etal. (1987)
Kralj and Stunja (1994)
Lalitha and Rani (1995)
Lan etal. (1995)
Lemaire etal. (1993)
Livingstone et al. (1992)
Low and Sin (1995, 1996)
Micallef and Tyler (1990)
Montagnese et al. (1993)
Murataetal. (1996)
Nakonieczny (1993)
Neuhierl and Boeck (1996)
Nigro etal (1992, 1994)
Norheim and Borch-Iohnsen (1990)
Norheimetal. (1991)
OBrienetal. (1995)
Olson and Christensen (1980)
Overbaugh and Fall (1985)
Palmisano et al. (1995)
Patel etal. (1990)
Patel and Chandy (1987)
Perez etal. (1990)
Perez-Trigo et al. (1995)
Phadnisetal. (1988)
Price and Harrison (1988)
Rady etal. (1992)
Rani and Lalitha (1996)
Regolietal. (1997)
Schmidt etal. (1985)
Schmittetal. (1993)
Segneretal. (1994)
Sen etal. (1995)
Shigeoka etal. (1990, 1991)
Siwicki etal. (1994)
Srivastava and Srivastava (1995)
Sun etal. (1995)
Takedaetal. (1992a,b,(1993,
1997)
Treuhardt(1992)
Vazquez etal. (1994)
Veena etal. (1997)
Wise etal. (1993a,b)
Wong and Oliveira (1991)
Yokotaetal. (1988)
Test procedures test material or results were not adequately described by Botsford (1997), Botsford et al.
(1997, 1998), Bovee (1978), Gissel-Nielsen and Gissel-Nielsen (1973, 1978), Greenberg and Kopec
(1986), Mauk (2001), and Nassos et al. (1980) or when the test media contained an excessive amount
(>200 Og/L) of EDTA (Riedel and Sanders (1996).
G-5
Draft November 12, 2004
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Some data obtained from tests conducted with just one exposure concentration to evaluate acute or chronic
toxicity were not used (e.g., Bennett 1988; Heinz and Hoffman 1998; Munawar et al. 1987; Pagano et al.
1986; Wolfenberger 1986).
Kaiser (1980) calculated the toxicities of selenium(IV) and selenium(VI) tcDaphnia magna based on
physiochemical parameters. Kumar (1964) did not include a control treatment in the toxicity tests. The
daphnids were probably stressed by crowding in the tests reported be Schultz et al. (1980). Siebers and
Ehlers (1979) exposed too few test organisms as did Owsley (1984) in some tests.
Data Were Not Used When the Organisms Were Exposed to Selenium by Food or by Gavage or Injection
Frankenberger and Engberg (in Hoffman et al. (1991, Malchow et al. (1995)
press) 1992a,b,1996) ParipatananontandLovell(1997)
Hamilton (1999) Huerkamp et al. (1988) Sheline and Schmidt-Nielson
Hamilton and Lemly (1999) Mshamn et al. (1990) (1977)
Heinz and Sanderson (1990) Kleinow (1984) Stanley et al. (1994, 1996)
Heinz et al. (1990, 1996) Kleinow and Brooks (1986a,b) Wiemeyer and Hoffman (1996)
Hilton et al. (1982) Lemly (1996, 1997, 1999) Wilson et al. (1997)
Hoffman and Heinz (1988) Lorentzen et al. (1994)
Maageand Waagboe (1990)
BCFs and BAFs from laboratory tests were not used when the tests were static or when the concentration
of selenium in the test solution was not adequately measured or varied too much (Nassos et al. 1980; Ornes
et al. 1991; Riedel et al. 1991; Sharma and Davis 1980; Vandermeulen and Foda 1988).
Selenium Concentrations Reported in Wild Aquatic Organisms Were Insufficient to Calculate BAF
Abdel-Moati and Atta (1991) Ambulkar et al. (1995) Arway (1988)
Adeloju and Young (1994) Amiard et al. (1991, 1993) Ashton (1991)
Aguirre et al. (1994) Andersen and Depledge (1997) Augier et al. (1991, 1993, 1995a,b)
Akesson and Srikumar (1994) Andreev and Simeonov (1992) Augspurger et al. (1998)
Aksnes et al. (1983) Angulo (1996) Avery et al. (1996)
Allen and Wilson (1990) Arrula et al. (1996) Badsha and Goldspink (1988)
G-6 DraftNovember 12,2004
-------
Baines and Fisher (2001)
Baldwin and Maher (1997)
Baldwin et al. (1996)
Barghigiani(1993)
Barghigiani et al. (1991)
Baron etal. (1997)
Batley(1987)
Baumann and Gillespie (1986)
Baumann and May (1984)
Beal(1974)
Beck etal. (1997)
Beland etal. (1993)
Beliaeffetal. (1997)
Bell and Cowey (1989)
Benemariya et al. (1991)
Berry etal. (1997)
Bertram et al. (1986)
Besseretal. (1994, 1993)
Birkner(1978)
Boisson and Romeo (1996)
Bowerman et al. (1994)
Braune eta. (1991)
Brezina and Arnold (1977)
Brugmann and Hennings (1994)
Brugmann and Lange (1988)
Brumbaugh and Walther (1991)
Burger (1992, 1994, 1995, 1996,
1997a,b)
Burger and Gochfeld (1992a,b,
1993, 1995 ab, 1996, 1997)
Burger et al. (1992a,b,c,1993,
1994a,b)
Byrne and DeLeon (1986)
Byrne etal. (1985)
Cantillo etal. (1997)
Capar and Yess (1996)
Capellietal. (1987, 1991)
Cappon(1984)
Cappon and Smith (1981)
(1982a,b)
Cardellicchio(1995)
Carell etal. (1987)
Carter and Porter (1997)
Caurantetal. (1994, 1996)
Chau and Riley (1965)
Chiang etal. (1994)
Chou and Uthe (1991)
Chvojka(1988)
Chvojkaetal. (1990)
Clifford and Harrison (1988)
Collins (1992)
Combs etal. (1996)
Cossonetal. (1988)
Courtney etal. (1994)
Crowys etal. (1994)
Crutchfield (2000)
Cumbie and Van Horn (1978)
Currey etal. (1992)
Custer and Hohman (1994)
Custer and Mitchell (1991, 1993)
Custer etal. (1997)
Dabeka and McKenzie (1991)
Davoren(1986)
Deaker and Maher (1997)
Demon etal. (1988)
Dietz etal. (1995, 1996)
Doherty etal. (1993)
Elliott and Scheuhammer (1997)
Eriksson et al. (1989)
Evans etal. (1993)
Felton and Mathews (1990)
Feltonetal. (1994)
Fitzsimmons et al. (1995)
Focardietal. (1985, 1988)
Fowler (1986)
Fowler etal. (1975, 1985)
France (1987)
Friberg(1988)
Froslieetal. (1985, 1987)
Gabrashanske and Daskalova
(1985)
Gabrashanska andNedeva (1994)
Galgan and Frank (1995)
Garcia - Hernandez et al. (2000)
Giardina etal. (1997)
Gillespie and Baumann (1986)
Gochfeld (1997)
Goede(1985, 1991, 1993a,b)
Goedeetal. (1989, 1993)
Goede and DeBruin (1984, 1985)
Goede and Wolterbeek (1993,
1994a,b)
Gras etal. (1992)
Greig and Jones (1976)
Gutenmann et al. (1988)
Gutierrez-Galindo et al. (1994)
Guven etal. (1992)
Halbrook etal. (1996)
Hall and Fisher (1985)
Hamilton and Waddell (1994)
Hamilton and Wiedmeyer (1990)
Hansenetal. (1990)
Hardiman and Pearson (1995)
Hargrave etal. (1992)
Harrison and Klaverkamp (1990)
Hasunuma et al. (1993)
Haynesetal. (1995)
Hein etal. (1994)
Heiny and Tate (1997)
Heinz (1993a)
Heinz and Fitzgerald (1993a,b)
Heit(1985)
Heit and Klusek (1985)
Heitetal. (1980, 1989)
G-7
Draft November 12, 2004
-------
Hellou et al. (1992a,b) (1996a,b)
Henny and Herron (1989)
Hodge etal. (1996)
Hilton etal. (1982)
Honda etal. (1986)
Hothem and Ohlendorf (1989)
Hothem and Welsh (1994b)
Hothem and Zador (1995)
Hothem etal. (1995)
Houpt etal. (1988)
Hunter etal. (1995, 1997)
Ibrahim and Farrag (1992)
Ibrahim and Mat (1995)
Ishikawaetal. (1993)
Itanoetal. (1984, 1985a,b)
Jarmanetal. (1996)
Johns etal. (1988)
Johnson (1987)
Jop etal. (1997)
Jorhemetal. (1994)
Julshamn et al. (1987)
Kai et al. (1986a,b, 1988, 1992a,b,
1996)
Kaiser etal. (1979)
Kalas etal. (1995)
Kidwell etal. (1995)
Koemanetal. (1973)
Kovacs etal. (1984)
Krogh and Scanes (1997)
Krushevska et al. (1996)
Lakshmanan and Stephen (1994)
Lalithaetal. (1994)
LamLeung et al. (1991)
Lanetal. (1994a,b)
Langlois and Langis (1995)
Larsen and Stuerup (1994)
Larsenetal. (1997)
Lauchli(1993)
Law etal. (1996)
Lee and Fisher (1992a,b, 1993)
Leighton and Wobeser (1994)
Leland and Scudder (1990)
Lemly(1985a, 1994)
Leonzio etal. (1986, 1989, 1992)
Leskinen et al. (1986)
Li etal. (1996)
Lie etal. (1994)
Liu etal. (1987)
Lizamaetal. (1989)
Lobeletal. (1989, 1991, 1992a,b)
Lonzarich etal. (1992)
Lourdesetal. (1990)
Lowe etal. (1985)
Lucas etal. (1970)
Lytle and Lytle (1982)
Mackey etal. (1996)
Maher(1987)
Maher etal. (1992, 1997)
Mann etal. (1988)
Mason et al. (2000)
Masuzawa et al. (1988)
Matsumoto(1991)
Mavenetal. (1995)
May and McKinney (1981)
Mcdowell et al. (1995)
McKenzie-Parnell et al. (1988)
Meadoretal. (1993)
Mehrle etal. (1982)
Meltzeretal. (1993)
Metcalfe-Smith et al. (1992, 1996)
Michotetal. (1994)
Mills etal. (1993)
Moharram et al. (1987)
Moller(1996)
Mora and Anderson (1995)
Moreraetal. (1997)
Muir etal. (1988)
Mutanenetal. (1986)
Nadkarni and Primack (1993)
Nakamoto and Hassler (1992)
Narasaki and Cao (1996)
Navarrete et al. (1990)
Nettleton et al. (1990)
Nicola etal. (1987)
Nielsen and Dietz (1990)
Norheim(1987)
Norheimetal. (1992)
Norrgren etal. (1993)
Norstrom etal. (1986)
OConner(1996)
OShea etal. (1984)
Oberetal. (1987)
Oehlenschlager(1997)
Ohlendorf (1986)
Ohlendorf and Harrison (1986)
Ohlendorf and Maron (1990)
Ohlendorf etal. (1986a,b, 1987,
1988a,b)
Okazaki and Panietz (1981)
Ostapczuketal. (1997)
Pakkala etal. (1972)
Pal etal. (1997)
Palawski et al. (1991)
Palmer-Locarnini and Presley
(1995)
Paludan-Miller et al. (1993)
Papadopoulou and Andreotis
(1985)
Park and Presley (1997)
Park etal. (1994)
Paveglio et al. (1994)
Payer and Runkel (1978)
Payer etal. (1976)
Pennington et al. (1982)
G-8
Draft November 12, 2004
-------
Presley et al. (1990)
Quevauviller et al. (1993a,b)
Ramos etal. (1992)
Raoetal. (1996)
Reinfelder and Fisher (1991)
Reinfelder et al. (1993, 1998)
Renzonietal. (1986)
Rigetetal. (1996)
Risenhoover(1989)
Roditi (2000)
Rouxetal. (1994)
Ruelle and Keenlyne (1993)
Sager and Cofield (1984)
Saiki(1986ab, 1987, 1990)
Saiki and Lowe (1987)
Saiki and May (1988)
Saiki and Palawski (1990)
Saiki etal. (1992, 1993)
Sanders and Gilmour (1994)
Scanes(1997)
Scheuhammer et al. (1988)
Schantz etal. (1997)
Schmitt and Brumbaugh (1990)
Schramel and Xu (1991)
Schuleretal. (1990)
Scott and Latshaw (1993)
Secoretal. (1993)
Seelyeetal. (1982)
Sharif etal. (1993)
Shen etal. (1997)
Shirasaki etal. (1996)
Shultz and Ito (1979)
Simopoulos(1997)
Skaareetal. (1990, 1994)
Smith and Flegal (1989)
Smith etal. (1992)
Sorensen(1988)
Sorensen and Bauer (1984a,b)
Sorensen and Bjerregaard (1991)
Sorensen et al. (1982, 1983, 1984)
Southworth et al. (2000)
Sparling and Lowe (1996)
Speyer(1980)
Steimle etal. (1994)
Stoeppleretal. (1988)
Stone etal. (1988)
Strippetal. (1990)
Sundarrao et al. (1991) (1992)
Svenssonetal. (1992)
Tabaka etal. (1996)
Talbot and Chang (1987)
Tallandini etal. (1996)
Tan and Marshall (1997)
Tang etal. (1997)
Tao etal. (1993)
Teherani(1987)
Teig en etal. (1993)
Thomas etal. (1999)
Tilbury etal. (1997)
Topcuoglu etal. (1990)
TranVan and Teherani (1988)
Trocine and Trefry (1996)
Uthe and Bigh (1971)
Vanderstoep etal. (1990)
Varanasi etal. (1993, 1994)
Vitaliano and Zdanowicz (1992)
Vlieg(1990)
Vlieg etal. (1993)
Vos etal. (1986)
Waddell and May (1995)
Wagemann(1988)
Wagemann and Stewart (1994)
Wagemann et al. (1988) (1996)
Walsh etal. (1977)
Wang (1996)
Ward and Flick (1990)
Warren etal. (1990)
Weber (1985)
Welsh and Maughan (1994)
Wen etal. (1997)
Wenzel and Gabrielsen (1995)
Whyte and Boutillier (1991)
Williams etal. (1994)
Wilson etal. (1992, 1997)
Winger and Andreasen (1985)
Winger etal. (1984, 1990)
Woock and Summers (1984)
Wren etal. (1987)
Wu and Huang (1991)
Yamaoka etal. (1996)
Yamazaki et al. (1996)
Yoshida and Yasumoto (1987)
Zattaetal. (1985)
Zeisleretal. (1988, 1993)
Zhou and Liu (1997)
G-9
Draft November 12, 2004
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APPENDIX H
DATA USED IN REGRESSION ANALYSIS OF SELENIUM IN WHOLE-BODY
FISH TISSUE WITH SELENIUM IN MUSCLE, OVARY AND LIVER TISSUES
H-l Draft November 12, 2004
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DATA USED IN REGRESSION ANALYSIS OF SELENIUM IN WHOLE-BODY
FISH TISSUE WITH SELENIUM IN MUSCLE, OVARY AND LIVER TISSUES
Quantile regression was used to estimate median concentrations of selenium in the whole body as a
function of selenium concentration in selected tissues (Tables H-2, H-3, H-4). Only data where
organisms were exposed to selenium in water and in diet or in only diet were considered for analysis.
Quantile regression fits a curve to the data such that a selected proportion i (the quantile) of observations
are below and the complementary fraction 1- 1 is above it (Koenker and Basset 1978). Estimates of
model parameters minimize the sum of weighted absolute deviations. In contrast, ordinary least squares
minimize the sum of squared deviations. Least absolute deviation is less sensitive to outliers than least
squares (Birkes and Dodge 1993). Other desired properties of quantile regression include: it is
equivariant to scale changes, location shift, and monotonic transformations (Koenker and Basset 1978,
Cade et al. 1999). Furthermore, with rank-score statistics it is possible to test hypotheses and build
confidence intervals for parameters of linear models fit to data with heteroscedastic errors (Koenker
1994, Koenker and Machado 1999). The rank-score test does not have to assume homogeneous error
distributions because the statistic is based on signs of residuals and not their size (Koenker and Machado
1999). For introductory presentations of quantile regression see Cade et al. (1999), Koenker and Hallock
(2001), and Cade & Noon (2003). All quantile regressions reported here were performed using the R
software (Ihaka & Gentleman 1996) version 1.8.0.
As the exact form of the relationship between selenium concentrations in the whole body ([Se]WB) and in
tissues ([Se]Tlssue) is not known, we considered three candidate models :
I) [Se]WB = a.
II) [Se]WB = a + b [Se]Tlssue and
III) [Se]WB = exp(a + Mn([Se]Tlssue))
where a and b are the model parameters we wish to estimate. Model (I) implicitly assumes that selenium
concentrations in the whole body are independent of selenium concentrations in liver, muscle, or ovary
tissues. Model (II) projects selenium concentrations in the whole body as a linear function of selenium
concentrations in a tissue. Model (IE) estimates selenium concentrations in the whole body as an
exponential function of the logarithm of selenium concentrations in a tissue. This model is derived from
the assumption of a linear relationship between the natural logarithms of [Se]WB and [Se]Tlssue.
Selection of the best model(s) considers both the fit and number of parameters. Models with greater
number of parameters generally fit the data better, but such reduction in bias is invariably associated wilh
an increase in variance of parameter estimates (Burnham and Anderson 2002). Model selection methods
attempt to find a parsimonious model with the proper tradeoff between bias and variance. We apply the
information theoretic approach for model selection (Burnham and Anderson 2002). It is based on the
Kullback-Leibler information, I(f,g), which expresses the information lost when model g is used to
estimate the full reality/ Obviously, the full reality is never known, but an estimate of the relative
distance from reality can be estimated by the Akaike Information Criterion (AIC, Akaike 1973)
AIC = -2 ln(a?(parameters|data)) + 2k
H-2 Draft November 12, 2004
-------
where k is the number of parameters in the model and S£ (parameters|data) is the maximized likelihood of
parameter estimates for the available data.. The AIC is a poor estimator ofl(f,g) when nlk < 40 (n is the
sample size). In such instances, a second-order version of AIC, AICC, is recommended (Hurvich and Tsai
1989):
AICC = -2 ln(a?(parameters|data)) + 2k
Hurvich and Tsai (1990) demonstrated that the modified version of AIC c for least absolute
deviation(LlAICc) provides an unbiased estimator for the Kullback-Leibler information, but the small
sample criterion for normal least squares regression, which is less computationally demanding, performs
equally well
AIC = «lno-2 + 2k
,n-k-\)
where a2 is estimated as the sum of squared residual s divided by n. For the least absolute deviation
regression, a2 is estimated as (SWAD/«)2, thus AICc is computed by the expression
The AIC and AICC are used to rank candidate models. Comparisons among the M ranked
candidates are based on the Akaike weight (w), which represents the likelihood of a model given the data
f-M
exp -r-
w. =
M f
S
exp
i-i \
where A, is the difference in AIC (AICC) between model /' and the model with the lowest AIC (AICC)
value. Weights for all candidate models sum to 1. For each model, we computed the sum of weighted
absolute deviations (SWAD), AICC and the Akaike weight (Table H-l).
The linear model (II) was selected the best among the three candidate functions for projecting
concentrations of selenium in the whole body as a function of selenium concentrations in the liver (Table
H-l). The exponential model (III) was selected the best for projections based on concentrations of
selenium in muscles and ovaries. However, fits of models Hand III to ovary data had similar weights. As
the best model may not explain much of the observed variation in the data, we calculated coefficients of
determination (R1), defined as
R1 = 1 - (SAF/SAR)
H-3 Draft November 12, 2004
-------
where SAP and SAR are the sum of weighted absolute deviations for the full and reduced models,
respectively (Cade and Richards 1996). Coefficients of determination for models II and IE were also
very similar, suggesting that both models are equally effective in predicting concentrations of selenium in
the whole body as a function of selenium concentrations in ovaries. With such knowledge, we opted to
use the linear model (II) because it is easier to compute. The exponential model for muscle presented the
highest coefficient of determination (0.77), indicating that samples of selenium concentrations from this
tissue are more effective predictors than samples from liver and ovaries. The fitted quantile regression
curves are shown in figure 5 of the selenium document.
TableH- 1. Number of parameters (k), sum of weighted absolute deviations (SWAD), second-order
Akaike Information Criterion (AICC), differences between the model AICC and the lowest AICC of all
candidate models (Delta), weight (w), rank (by weight), and coefficient of determination (R) for three
candidate models to project selenium concentrations in the whole body as a function of selenium
concentrations in a selected tissue.
Tissue: Muscle (n = 21)
Model
[Se]WB = a
[Se]WB = a + 6[Se]Tlssue
[Se]WB = exp(a + 6*ln([Se]Tlssue))
k
2
3
3
SWAD
66.00
16.84
15.10
AICc
52.76
-1.85
-6.43
Delta
59.20
4.59
0.00
Weight
1.27e-13
9.17e-02
9.08e-01
Rank
3
2
1
R1
0.74
0.77
Tissue: Ovary (n = 23)
Model
[Se]WB = a
[Se]WB = a + b [Se]Tlssue
[Se]WB = exp(a + 6*ln([Se]Tlssue))
k
2
3
3
SWAD
73.95
25.20
25.18
AICc
58.32
11.46
11.43
Delta
46.89
0.03
0.00
Weight
3.31e-ll
4.97e-01
5.03e-01
Rank
3
2
1
R1
0.66
0.66
Tissue: Liver (n = 26)
Model
[Se]WB = a
[Se]WB = a + b [Se]Tlssue
[Se]WB = exp(a + />ln([Se]Tlssue))
k
2
3
3
SWAD
41.05
25.20
40.83
AICc
28.27
5.46
30.56
Delta
22.81
0.00
25.10
Weight
l.lle-05
9.99e-01
3.54e-06
Rank
3
1
2
R1
0.39
0.01
H-4
Draft November 12, 2004
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Table H-l. Whole body vs muscle
reference
species
site/treatment
Se in tissue, (ig/g dw
muscle whole body
Hermanutz etal. 1996 bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
Garcia-Hernandez 2000 tilapia
carp
LM bass
I control-down
I 10 (ig/L-down
II control-up
II control-down
II 2.5 (ig/L-up
II 2.5 (ig/L-down
II 10 (ig/L-up
II 10 (ig/L-down
II rec 30-up
II rec 30-down
III control-up
III control-down
III rec 2. 5 -up
III rec 2. 5 -down
III rec 10-up
III rec 10-down
III rec 30-up
III rec 30-down
Cienega de Santa Cl
Cienega de Santa Cl
Cienega de Santa Cl
2.05
20.55
1.9
2.25
3.5
6.9
17.55
44.7
12.45
39.6
3.35
3.2
5.25
6.1
12.45
18.6
7.75
15.05
3.5
4.6
5.4
1.95
22.85
2.45
1.95
3.5
6.15
15.45
26.45
11.85
30.6
3.35
2.3
6.3
5.3
12
13
8.35
17.35
3
3.3
5.1
H-5
Draft November 12, 2004
-------
Table H-2. Whole Body vs Ovary
reference
Coyle 1993
Hermanutz etal. 1996
species
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
site/treatment
control
control + water Se
4.6 (ig/g diet
8.4 (ig/g diet
16.8 (ig/g diet
33.3 (ig/g diet
I control-down
I 10 (ig/L-down
II control-up
II control-down
II 2.5 (ig/L-up
II 2.5 (ig/L-down
II 10 (ig/L-up
II 10 (ig/L-down
II rec 30-up
II rec 30-down
III control-down
III rec 2. 5 -up
III rec 2. 5 -down
III rec 10-up
III rec 10-down
III rec 30-up
III rec 30-down
Se in tissue, (ig/g dw
ovary whole body
2.1
2.1
8.3
12.5
25
41
0.35
20.05
5.25
3.85
10.1
12.35
34.8
50.5
29.35
66
5.3
8.4
9.5
31.15
19.55
17.85
19.1
0.9
0.9
2.9
4.9
7.2
16
1.95
22.85
2.45
1.95
3.5
6.15
15.45
26.45
11.85
30.6
2.3
6.3
5.3
12
13
8.35
17.35
H-6
Draft November 12, 2004
-------
Table H-3. Whole body vs liver
reference
Bryson 1985-84
Hermanutz etal. 1996
Garcia-Hernandez 2000
species
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
bluegill
carp
LM bass
site/treatment
control
Se -plankton diet
Selenite diet
Se-cysteine diet
Se-cysteine 2X diet
Se-methionine diet
I control-down
I 10 (ig/L-down
II control-up
II control-down
II 2.5 (ig/L-up
II 2.5 (ig/L-down
II 10 (ig/L-up
II 10 (ig/L-down
II rec 30-up
II rec 30-down
III control-up
III control-down
III rec 2. 5 -up
III rec 2. 5 -down
III rec 1 0-up
III rec 10-down
III rec 30-up
III rec 30-down
Cienega de Santa Cl
Cienega de Santa Cl
Se in tissue, (ig/g dw
liver whole body
3.9
9.1
11
9.23
16.33
10.85
5.4
36.05
13.2
7.2
29.2
26.45
119
68.5
64
100.5
9.95
9.4
13.85
16.3
33.25
37.15
21
31.9
8.2
4.7
0.45
2.35
1.21
2.16
3.74
2.46
1.95
22.85
2.45
1.95
3.5
6.15
15.45
26.45
11.85
30.6
3.35
2.3
6.3
5.3
12
13
8.35
17.35
3.3
5.1
H-7
Draft November 12, 2004
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APPENDIX I
SUMMARIES OF CHRONIC STUDIES CONSIDERED FOR FCV DERIVATION
1-1 Draft November 12, 2004
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Dobbs, M.G., D.S. Cherry, and J. Cairns, Jr. 1996. Toxicity and bioaccumulation of selenium to a
three-trophic level food chain. Environ. Toxicol. Chem. 15:340-347.
Test Organism:
Exposure Route:
Rotifer (Brachionus calyciflorus), and fathead minnow (Pimephales promelas)
12 to 24 hr-old at start.
Dietary and waterborne
Water
Filtered and sterilized natural creek water supplemented with nutrients
(Modified Guillard's Woods Hole Marine Biological Laboratory algal culture
medium) for algal growth. Sodium selenate (Na2SeO4) was added to test water
to obtain nominal concentrations of 100,200, or 400 (ig Se/L. Concentrations
remained stable and equal in each trophic level.
Control Diet
No selenium was added to the water medium for the alga; green alga was free of
selenium for the rotifer; and rotifers were free of selenium for the fathead
minnow.
Selenium Diet
Sodium selenate was added to the culture medium for the alga; green alga
thereby contained a body burden for the rotifer; and rotifers thereby contained a
body burden for the fathead minnow.
Dietary Treatments: Each trophic level had a different treatment. The green alga was exposed
directly from the water (1,108.1, 204.9, 397.6 (ig total Se/L); rotifers were
exposed from the water (1, 108.1, 204.9, 393.0 (ig total Se/L) and the green alga
as food (2.5, 33, 40, 50 (ig Se/g dry wt); and the fathead minnow were exposed
from water (1, 108.1, 204.9,393.0 (ig total Se/L) and the rotifer as food (2.5, 47,
53,60(igSe/gdrywt).
Test Duration:
Study Design:
25 days
A flow-through system utilizing a stock solution of filtered and sterilized creek
water controlled at 25°C was used to expose three trophic levels of organisms.
Approximately one liter of media was pumped from the algal chamber into the
rotifer chamber each day. A cell density between 3 and 6 x 106 cells/ml was
delivered to the rotifer chambers. Rotifers were started at a density of 151.4 ±
7.7 females/ml and one liter/day of rotifers containing culture water was
intermittently pumped into the minnow chamber. (B. calyciflorus have a life
span of about 7 days at 25° C.) The pump was necessary to overcome the
swimming ability of rotifers to avoid an overflow tube. Larval fathead minnows
(35/chamber) were prevented from escaping by a screened overflow. Chambers
were cleaned daily and aeration was provided. All chambers were duplicated for
test replication and water was measured for selenium on days 0, 2, 6,7, 11, 14,
17, 20, and 24. All algal and rotifer biomass and selenium samples were made
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Draft November 12, 2004
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Effects Data:
on these days. Fathead minnow chambers were measured forbiomass, dissolved
selenium, and tissue selenium concentrations of days 0, 7, 11, 14,20, and 24.
Additional measurements were made in the 200 (ig Se/L test chambers on the
fathead minnow on day 16. Selenium concentrations were maintained near the
nominal concentrations and the standard deviation of mean concentrations was
less than 4 percent.
Rotifers. Rotifers did not grow well and demonstrated reduced survival at all
selenium exposure concentrations during the 25 day test. By test day 7 only the
lowest test concentration (108.1 (ig/L) had surviving rotifers which showed a
decrease in selenium content from test days 18 through 25. A reduction in
rotifer biomass was discernable by test day 4 in the selenium treatments and
since all test concentrations had viable rotifer populations present, the effect
level was calculated using these data.
Effect of Dietary and Waterborne Selenium on Rotifers after 4 Days Exposure
Se in water, (jg/L
1
108.1
202.4
393
Se in diet, (ig/g dw
2.5
33
40
50
Se in rotifer tissue,
Mg/g dw
2.5
40
54
75
rotifer biomass, mg/ml
dw
0.028
0.025
0.011
0.003
Fathead minnows. Due to the reduction of rotifer biomass in the higher test
concentrations, fish mortality and reduction in fish growth observed in the latter
days of the test was difficult to discern between effects from starvation and
selenium toxicity. The data from test day 8 was selected for determining the
effect of selenium on fathead minnows because starvation could be excluded as a
variable.
Effect of Dietary and Waterborne Selenium on Larval Fathead Minnows after 8 Days Exposure
Se in water, (jg/L
1
108.1
202.4
393
Se in diet, (ig/g dw
2.5
47
53
60
Se in fathead minnow
tissue, (ig/g dw
2.5
45
75
73
average fish weight,
mg dw
0.8
0.7
0.4
0.2
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Draft November 12, 2004
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Chronic Value:
Rotifers 42.36 (ig Se/g dw (EQ0)
Fish < 73 (ig Se/g dw (LOAEC)-not amenable to statistical treatment; the LOAEC
was based on the observation that a >50 percent reduction in mean fish weight
occurred at this tissue concentration.
Rotifer (Dobbs 1996)
0.05
0.04 -
E
O)
E 0.03 -
DJ
0.02 -
0.01
0.00
1.0
F
2 3 4567
Tissue
1QQ
2 3 4567
1-4
Draft November 12, 2004
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Hamilton, S.J., K.J. Buhl, N.L. Faerber,R.H. Wiedermeyer and F.A. Bullard. 1990. Toxicity of
organic selenium in the diet of chinook salmon. Environ. Toxicol. Chem. 9:347-358.
Test Organism:
Exposure Route:
Dietary Treatments:
Chinook salmon (Oncorhynchus tshawytschaWalbaum; swim-up larvae)
Dietary only
Control Diet
Oregon moist pellet diet where over half of the salmon meal was replaced with
meal from low-selenium mosquitofish (1.0 (ig Se/g dw) collected from a
reference site.
Selenium Diet # 1
Oregon moist pellet diet where over half of the salmon meal was replaced with
meal from high-selenium mosquitofish (35.4 (ig Se/g dw) collected from the San
Luis Drain, CA, termed SLD diet.
Selenium Diet #2
Oregon moist pellet diet where over half of the salmon meal was replaced with
meal from low-selenium mosquitofish same as in the control diet, but fortified
with seleno-DL-methionine (35.5 pg Se/g dw), termed SeMet diet.
Each selenium diet was formulated to contain about 36 (ig Se/g dw as the high
exposure treatment. The remaining treatments were achieved by thoroughly
mixing appropriate amounts of high-exposure treatment diet with control diet to
yield the following nominal concentrations (3, 5, 10, and 18 (ig Se/g dw).
Test Duration: 90 days
Study Design: Each dietary treatment was fed twice each day to swim-up larvae (n=100) in each of two
replicate aquaria that received 1 L of replacement water (a reconstituted experimental
water that simulated in quality a 1:37 dilution of water from the San Luis Drain, CA
minus the trace elements) every 15 minutes (flow-through design). Mortality was
recorded daily. Growth was evaluated at 30-day intervals by measuring the total lengths
and wet weights of two subsets of individual fish (n=10x2) held in separate 11.5 L
growth chambers within each replicate aquarium. Tissue samples were collected for
whole-body selenium determinations (dry wt. basis) at 30-day intervals throughout the
study; 10, 5, and 2 fish were sampled from each duplicate treatment after 30, 60, and 90
days of exposure, respectively. Concentrations of selenium measured in water were
below the limit of detection (1.5-3.1 pg/L) in all dietary selenium exposure
concentrations.
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Draft November 12, 2004
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Effects Data:
The magnitude of reduced growth was most evident in the weight of the fish,
although total length was significantly reduced in fish fed high Se-laden diets as
well. The effect of increasing dietary selenium on mean larval weight was
similar in both the SLD and seleno^nethionine diets.
Effect of San Luis Drain Diet on Growth and Survival of Chinook Salmon Larvae after 60 Days
Se in diet, (ig/g dw
1
3.2
5.3
9.6
18.2
35.4
Se in chinook salmon,
Mg/g dw
0.9
3.3
4.5
8.4
13.3
29.4
mean larval weight, g
3.35
2.68
2.76
2.8
2.62
1.4
survival, %
99
97.3
93
95
92.4
89
Effect of Seleno-methionine Diet on Growth and Survival of Chinook Salmon Larvae after 60 Days
Se in diet, (ig/g dw
1
3.2
5.3
9.6
18.2
35.4
Se in chinook salmon,
Mg/g dw
0.9
2
3.1
5.3
10.4
23.4
mean larval weight, g
3.35
3.08
3.22
3.07
2.61
1.25
survival, %
99
100
95
94.1
92.4
62.5
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Draft November 12, 2004
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Chronic Value:
Due to unacceptable control mortality of swim-up larvae in control treatments
after 90 days (33.3 percent - SLD diet; 27.5 percent - SeMet diet), chronic values
had to be determined from respective values reported after 60 days (tables
above).
Analysis of the elemental composition of the SLD diet indicated that B, Cr, Fe,
Mg, Ni and Sr were slightly elevated compared to the control and SeMet diets.
No additional analyses were performed to determine the presence of other
possible contaminants, i.e., pesticides.
Diet type
SLD
SeMet
EC20 values
Survival
(after 60 d of exposure)
Tissue Se
((ig/g dw)
NAa
NAa
Growth
(after 60 d of exposure)
Tissue Se
((ig/g dw)
15.74
10.47
The EC20 values for survival of swim-up larvae versus levels of selenium for the SLD and SeMet
dietary exposure could not be estimated using non-linear regression.
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Draft November 12, 2004
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Chinook Salmon
SLD Diet - 60 Days (Hamilton et al.1990)
m 2
"3
oJ-
1.0
2 3456781QQ 2 3
Tissue Se[^g/g dw]
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Draft November 12, 2004
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Chinook Salmon
SeMet Diet - 60 Days (Hamilton et al. 1990)
3 -
2 -
1 -
0 J-
1.0
2 3 45678-|QQ
Tissue Se[fig/g dw]
2 3
1-9
Draft November 12, 2004
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Hilton, J.W. and P.V. Hodson. 1983. Effect of increased dietary carbohydrate on selenium metabolism
and toxicity in rainbow trout (Salmo gairdnerf). J. Nutr. 113:1241-1248.
Test Organism:
Exposure Route:
Test Treatments:
Test Duration:
Study Design:
Effects Data:
Rainbow trout (Oncorhynchus mykiss; juvenile; approx. 0.6 g each)
Dietary only
Low carbohydrate diet (LCD)
This diet contained capelin oil at 11 percent of the diet with cellulose as the
filler.
High carbohydrate diet (HCD)
This diet contained cerelose at 25 percent of the diet with cellulose as the filler.
For both diets, the selenium was supplemented as sodium selenite which was
mixed with cellulose and then added to the diet as a selenium premix.
The two diets were supplemented with selenium (as sodium selenite) at the rate
of 0, 5, or 10 (ig/g dw to make up the six different dietary selenium treatments (n
= 3 low carbohydrate diet; n= 3 high carbohydrate diet). The six diets were fed
to duplicate groups of 100 fish. The trout were fed to satiation 3-6 times per
day. Measured concentrations of selenium in the low carbohydrate diet were:
0.6 (control), 6.6, and 11.4 (ig/gdw, and the measured concentrations of
selenium in the high carbohydrate diet were: 0.7 (control), 6.6, and 11.8 (ig/g
dw. The tanks received a continuous flow of water with a flow rate of 3-4 Liters
per minute.
16 weeks
Body weights, feed:gain ratios, and total mortalities were determined after each
28-day interval. After 16 weeks, approximately 20 fish were randomly removed
from each tank, weighed, and blood was collected for hemoglobin, hematocrit,
and plasma glucose, protein, and calcium determination. The livers and kidneys
were then dissected. The livers were assayed for glycogen content, and samples
of both liver and kidney were assayed for selenium content. Additional
subsamples offish were sacrificed and assayed for selenium content and for ash,
crude protein, and moisture content (n=6 per treatment). Finally, 30 fish were
killed, their livers and kidneys dissected, and analyzed for Ca, Cu, Fe, Mg, P,
and Zn content.
The only overt sign of selenium toxicity was food avoidance observed in trout
fed the highest selenium content in both low and high carbohydrate diets, which
led to significantly reduced body weight after 16 weeks. There were no
significant differences detected between treatment groups in hematological
parameters. Kidney, liver, and carcass selenium levels increased with increasing
selenium content of the diet, however, only the liver selenium concentrations
were significantly affected by dietary selenium level, dietary carbohydrate level,
and the interaction between the two treatments. Mineral analysis of the kidney
1-10
Draft November 12, 2004
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showed significantly higher levels of calcium and phosphorous in trout reared on
the two highest levels of dietary selenium. Concentrations of copper in the liver
increased significantly with increasing dietary selenium levels and decreasing
dietary carbohydrate levels.
Effect of Selenium in Low carbohydrate Diet to Rainbow Trout
Se in diet, (ig/g dw
0.6
6.6
11.4
Se in trout liver, (ig/g dw
0.8
38.3
49.3
trout weight, kg/ 100 fish
3.3
3.3
1.8
Effect of Selenium in High carbohydrate Diet to Rainbow Trout
Se in diet, (ig/g dw
0.7
6.6
11.8
Se in trout liver, (ig/g dw
0.6
21.0
71.7
trout weight, kg/100 fish
2.7
2.3
1.4
Chronic Value:
The MATC estimated for growth of rainbow trout relative to final concentration
of selenium in liver tissue of trout reared on the low carbohydrate diet is the GM
of 38.3 (NOAEC)and 49.3 (LOAEC) (ig/gdw, or 43.45 (ig/g dw. The MATC
estimated for growth of rainbow trout relative to final concentration of selenium
in liver tissue of trout reared on the high carbohydrate diet is the GM of 21.0
(NOAEC) and 71.7 (LOAEC) (ig/g dw, or 38.80 (ig/g dw. Using equation HI in
the text to convert this selenium concentration in liver tissue to a concentration
of selenium in whole-body, the MATC for rainbow trout exposed to selenium in
food with low carbohydrate content becomes 13.08 (ig Se/g dw., whereas the
MATC for rainbow trout exposed to selenium in food with high carbohydrate
content becomes 11.65 (ig Se/g dw. The latter value is selected as 1he chronic
value for the study.
EC20 values could not be determined for this study. Data did not meet minimum
requirements for analysis.
1-11
Draft November 12, 2004
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Hicks, B.D., J.W. Hilton, and H.W. Ferguson. 1984. Influence of dietary selenium on the occurrence
of nephrocalcinosis in the rainbow trout, Salmo gairdneri Richardson. J. Fish Diseases. 7:379-389.
(Note: These data are the exact same as reported for the low carbohydrate diet in Hilton and Hodson
1983, with the addition of prevalence of nephrocalcinosis occurring in trout after 16 to 20 weeks of
consuming the contaminated test diets).
Test Organism:
Exposure Route:
Test Treatments:
Rainbow trout (Oncorhynchus mykiss; juvenile; approx. 0.6 g each)
Dietary only
This diet contained capelin oil at 11 percent of the diet with cellulose as the
filler. The selenium was supplemented as sodium selenite which was mixed
with cellulose and then added to the diet as a selenium premix.
The test diet was supplemented with selenium (as sodium selenite) at the rate of
0, 5, or 10 (ig/g dw to make up the three different dietary selenium treatments.
The three diets were fed to duplicate groups of 100 fish. The trout were fed to
satiation 3-6 times per day. Measured concentrations of selenium in the low
carbohydrate diet were: 0.6 (control), 6.6, and 11.4 (ig/g dw. The tanks received
a continuous flow of water with a flow rate of 3-4 Liters per minute.
Test Duration: 16 to 20 weeks
Study Design:
Effects Data:
Chronic Value:
See Hilton andHodson (1983). After 20 weeks on the test diets, ten fish were
randomly removed from each treatment. Tissues for histopathological
examination included the stomach, intestine and pyloric ceca (including
pancreas), spleen, liver, heart, kidney, skin, muscle, and gills.
Only effects of selenium on kidney tissue are included in the article. The
kidneys of the 10 trout fed the highest selenium content in the diet exhibited
normal appearance. Five of these trout exhibited precipitation of calcium in the
tubules with some epithelial necrosis, but no loss of epithelial continuity.
Extensive mineralized deposition of Ca within the tubules, tubular dilation and
necrosis of tubular epithelium, ulceration of tubules, and intestinal Ca
mineralization was observed in four of the ten fish.
Same as for growth of rainbow trout reported by Hilton and Hodson (1983). The
MATC estimated for growth of rainbow trout relative to final concentration of
selenium in liver tissue of trout reared on the low carbohydrate diet is the GM of
38.3 (NOAEC) and 49.3 (LOAEC) jig/g dw, or 43.45 (jg/g dw. Using equation
III to convert the selenium concentration in liver tissue to a concentration of
selenium in whole-body, the MATC becomes 13.08 (ig/g dw.
EC20 values could not be determined for this study. Data did not meet minimum
requirements for analysis.
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Draft November 12, 2004
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Hilton, J.W., P.V. Hodson, and S. J. Slinger. 1980. The requirements and toxicity of selenium in
rainbow trout (Salmo gairdnerf). J. Nutr. 110:2527-2535.
Test Organism:
Exposure Route:
Rainbow trout (Oncorhynchus mykiss; juvenile; approx. 1.28 g each)
Dietary only
A casien-torula yeast diet was formulated to contain geometrically increasing
levels of selenium from 0 to 15 (ig/g dw. The selenium was supplemented as
sodium selenite which was mixed with cellulose and then added to the diet as a
selenium premix.
Test Duration: 20 weeks
Study Design:
Effects Data:
Six test diets were fed to triplicate groups of 75 fish. The trout were fed to
satiation 34 times per day, 6 days per week, with one feeding on the seventh
day. Measured concentrations of selenium in the diet were: 0.07 (control), 0.15,
0.38, 1.25, 3.67, and 13.06 (ig/g dw. The tanks received a continuous flow of
dechlorinated tap water from the City of Burlinton, Ontario municipal water
supply. The waterborne selenium content of this water was 0.4 (ig/L. During
the experiment, the fish were weighed every 2 weeks with the feeding level
adjusted accordingly. Mortalities were noted daily and the feed consumption for
each treatment was recorded weekly. After 4 and 16 weeks, three to six fish
were randomly removed from each tank, sacrificed, and their livers and kidneys
removed and weighed. An additional three to six fish were then obtained from
each treatment, killed, and prepared for tissue analysis. Organs and carcasses
were freeze-dried for determination of selenium concentration. After 16 weeks,
three more fish were removed. Kidney, liver, spleen and dorsal muscle tissue
was dissected for examination of histopathology. At the end of 8 and 16 weeks,
four to five fish were removed, sacrificed, and a blood sample was taken for
hematological measurements (hematocrit, red blood cell count, and blood iron
concentration). After 20 weeks, three to four more fish were removed,
sacrificed, and a blood sample was taken for measurement of glutathione
peroxidase activity.
There were no significant differences detected between treatment groups in
histopathology, hematology, or plasma glutathione peroxidase activity. Trout
raised on the highest dietary level of selenium (13.06 (ig/g dw) had a
significantly lower body weight and a higher number of mortalities (10.7;
expressed as number per 10,000 fish days) than trout from the other treatments
levels after 20 weeks of exposure.
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Draft November 12, 2004
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Effects on Juvenile Rainbow Trout
Se in diet, (ig/g dw
0.07
0.15
0.38
1.25
3.67
13.06
Se in Liver, (ig/g dw
0.6
0.95
2.4
11
40
100
weight, g/fish
3.2
3.5
3.7
4.1
4.1
1.4
mortality*
0
0
0.6
0.6
0
10.7
* expressed as number per 10,000 fish-days
Chronic Value:
An MATC was preferred over regression analysis because of the large standard
error associated with the EC20 value. The MATC for the growth and survival of
juvenile trout based on selenium in liver tissue is the GM of the NOAEC (40
Hg/g dw) and the LOAEC (100 (ig/g dw), or 63.25 (ig Se/g dw. Using the
equation III in the text to convert the selenium concentration in liver tissue to a
concentration of selenium in whole-body tissue, the MATC becomes 19.16 (ig/g
dw.
1-14
Draft November 12, 2004
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Holm, J. 2002. Sublethal effects of selenium on rainbow trout (Oncorhynchus mykiss) and brook trout
(Salvelinus fontinalis). Masters Thesis. Department of Zoology, University of Manitoba, Winnipeg, MB.
Holm, J., V.P. Palace, K. Wautier, R.E. Evans, C.L. Baron, C. Podemski, P. Siwik and G. Sterling.
2003. An assessment of the development and survival of rainbow trout (Oncorhynchus mykiss) and
brook trout (Salvelinus fontinalis) exposed to elevated selenium in an area of active coal mining.
Proceedings of the 26th Annual Larval Fish Conference 2003, Bergen, Norway. ISBN 82-7461-059-B.
Test Organism:
Exposure Route:
Study Design:
Rainbow trout (Oncorhynchus mykiss; spawning adults) and brook trout
(Salvelinus fontinalis; spawning adults)
dietary and waterborne - field exposure
Total selenium concentrations measured at the high selenium site ranged from 6
to 32 (ig/L. Selenium was not measured at the reference streams; selenium
concentrations at reference locations in the area ranged from <0.5 to 2.2 (ig/L.
Spawning fish were collected at low selenium or reference streams (Deerlick
Creek and Cold Creek), a slightly elevated selenium stream (Gregg Creek), and
an elevated selenium stream (Luscar Creek) in the Northeastern slopes region of
Alberta, Canada. An active coal mine is the source of selenium in the elevated
streams. Eggs and milt from the spawning trout were expressed by light pressure
from abdomen. Individual clutches of eggs were fertilized from a composite
volume of milt derived from 3-5 males. Fertilized eggs from individual females
were reared to swim-up stage and examined for a number of parameters
including percent fertilization, mortality, edema, and deformities (craniofacial,
finfold, and spinal malformations). Similar studies were conducted in both 2000
and 2001. One notable difference is that the embryos were incubated at 8°C in
2000 and at 5°C in 2001. The authors noted that 5°C is a better representation of
the actual stream temperature during embryo development..
Effects Data :
Other than selenium, there were no significant differences in the concentrations
of other elements (Al, As, Sb, Ba, Be, Ni, B, Cd, Ca, Cr, Co, Cu, Fe, Pb, Li, Mg,
Mn, Hg, Mo, Ag, Sr, Tl, Th, Sn, Ti, U, V, Zn) in trout eggs between the low
level and elevated selenium streams. There are two ways to approach
determination of effects due to selenium in this study and both are presented
here. The first approach determines effects based on a comparison of average
conditions between streams (between streams approach). For example, if there
is a significant difference between the average frequency of deformities in a
contaminated stream and reference stream, the effect level for the between
streams approach would be the average concentration of selenium in the tissue
from the contaminated stream. The second approach evaluates individual
response variables (e.g., edema, deformities) against the individual selenium
tissue concentrations for the combined contaminated and reference stream data
set with each year (within streams approach). This approach, which results in
an EC20 value if the data meet the model assumptions, is explained in the
Calculations of Chronic Values section of the text.
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Draft November 12, 2004
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Between streams approach: For both rainbow and brook trout embryos, there
were no significant differences in fertilization, time to hatch and mortality
between the streams with elevated selenium and the reference streams in both
2000 and 2001. The frequency of embryonic effects were significantly greater in
the high selenium stream (Luscar Creek) in 2000. Rainbow trout embryos from
Luscar Creek had a greater frequency of craniofacial, skeletal andfmfold
deformities and edema; whereas brook trout from Luscar Creek had a greater
frequency of only craniofacial deformities (see Holm Tables 1 and 2 below). In
2001, however, there were no significant differences in embryonic deformities
between Luscar Creek and reference streams for both species of trout. The only
difference observed in 2001 was a greater frequency of fmfold deformities in
brook trout collected from Gregg Creek (intermediate selenium levels) relative to
the reference stream (see Holm table 2 below). All olher embryonic
measurements in 2001 were not significantly different between streams with
elevated selenium and reference streams. When the data for both years were
pooled, no significant effects were observed in embryos obtained from rainbow
and brook trout collected in Luscar Creek relative to reference streams (see
Holm Table 3).
Within streams approach. EC20 values could not be calculated for total
deformities or edema for the 2000 rainbow trout data because a logistic curve
could not be fitted to the data (see Holm Figures 1 and 2). For the 2001 data,
EC20 values could not be computed for edema and skeletal and fmfold
deformities for rainbow trout data because a logistic curve could not be fitted to
the data (see Holm Figures 3 and 4). Craniofacial deformities in the rainbow
embryo as a function of selenium in egg ww (2001 data) was fitted to a logistic
curve from which an EQ0 value was calculated (see Holm Figure 5). The brook
trout data for 2000 and 2001 were not suitable for fitting logistic curves (see
Holm Figure 6).
1-16 Draft November 12, 2004
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Holm Table 1
Mean embryo-larval parameters for rainbow trout collected from a high Se site (Luscar Creek), an intermediate Se site (Gregg River), and
reference sites (Deerlick Cieek and Wampus Creek) in northeastern Alberta over two consecutive years (mean ± SE). Values that are
significantly different at a = 0.05 are marked with different letters. (Table modified from Holm 2002)
Measurement
Se, egg, (ig/g ww
Se, adult muscle, (ig/g ww
na
% fertilization
% mortality
%CR
%SK
%FF
%ED
%TD
2000
Luscar
8.37 ± 1.62
1.50 ±0.28
297
79.8 ±4.3
3.3 ± 1.0
7.7±3.7b
13.8±5.6b
3.2±2.0b
30.8±27.4b
38.9±25.6b
Deerlick
2.05 ± 1.06
0.48 ±0.15
261
51.5 ± 10.9
0.7 ±0.4
0.2 ± 0.2C
0.7±0.5C
0.2±0.2C
0.2±0.2C
0.7±0.5C
2001
Luscar
6.49 ±0.89
NT
2021
81.5 ±5.0
27.8 ±7.3
14.7 ±3.4
19.4 ±8.2
6.8 ±3.0
19.9 ±8.5
ND
Gregg
6.65 ± 1.83
NT
720
79.4 ±5.2
38.3 ±13.7
11.7±2.7
11.1±2.3
15.5 ±6.6
13.9 ±5.3
ND
Deerlick
2.77 ±0.20
NT
1342
88.0 ±2.1
26.5 ±4.7
10.6 ± 1.9
15.6 ±4.7
4.0 ±0.9
10.8 ±2.5
ND
Wampus
2. 35 ±0.31
NT
209
94.0 ±4.8
4.2 ±0.8
12.0 ±4.1
4.9 ±4.9
1.5 ±0.2
7.5 ±0.4
ND
a number of fry to reach the swim-up stage
b and c statistically different values
CR = craniofacial defects, SK = skeletal defects, FF = fmfold defects, ED = edema, TD = total defects, NT = not tested, ND = not done
I-17 Draft November 12, 2004
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Holm Table 2
Mean embryo-larval parameters for brook trout collected from a high Se site (Luscar Creek), an intermediate Se site (Gregg River), and reference
sites (Cold Creek) in northeastern Albertaover two consecutive years (mean ± SE). Values that are significantly different at a = 0.05 are marked
with different letters. (Table modified from Holm 2002)
Site
Se, egg, (ig/g ww
Se, adult muscle, (ig/g ww
na
% fertilization
% mortality
%CR
%SK
%FF
%ED
%TD
2000
Luscar
6.37 ±0.78
3.79 ±0.51
4904
97.4 ±0.8
12.6 ±3. 8
13.6±3.5b
1.9 ±0.8
1.1±0.6
0.6 ±0.4
14.4±3.6b
Cold
1.35 ±0.24
0.55 ±0.10
1560
96.1 ± 1.2
9.3 ±2.4
3.0±0.5C
1.3 ±0.8
1.2 ±0.8
0.3 ±0.1
4.0±2.3C
2001
Luscar
8.02 ±0.77
NT
3440
87.2 ±2.6
2.9 ±0.8
5.6 ±3.2
2.1 ± 1.1
3.7 ± 1.8
0.4 ±0.1
ND
Gregg
6.88 ±0.51
NT
1892
85.2 ±5.4
2.9 ±0.9
2.12 ± 1.0
0.81 ±0.3
4.1±2.4C
0.3 ±0.2
ND
Cold
1.25 ±0.15
NT
1440
77.8 ± 14.2
3.7 ± 1.6
0.7 ±0.3
0.6 ±0.4
0.1±0.1b
1.7 ± 1.2
ND
a number of fry to reach the swim-up stage
b and c statistically different values
CR = craniofacial defects, SK = skeletal defects, FF = finfold defects, ED = edema, TD = total defects, ND = not done
1-18 Draft November 12, 2004
-------
Holm Table 3
Mean embryo-larval parameters for rainbow trout and brook trout collected from a high Se site (Luscar
Creek) and reference sites (Deerlick Creek and Cold Creek) in northeastern Alberta over two consecutive
years, combined over both years of the study by site (mean ± SE). Values that are significantly different at
a = 0.05 are marked with different letters. (Table modified from Holm 2002)
Measurement
Se, egg, |ig/g
ww
na
% fertilization
% mortality
%CR
%SK
%FF
%ED
Rainbow Trout
Luscar
6.92 ±0.78
2318
81.1±3.9
22.2 ±6.3
13.1 ±3.2
18.1 ±6.3
6.0 ±2.4
22.4 ±8. 5
Deerlick
2.56 ±0.32
1603
77.6 ±5.6
19.1 ±4.6
7.6 ±7.1
11.4±3.8
2.9 ±0.8
7.8 ±2.2
Brook Trout
Luscar
7.20 ±0.56
8344
92.3 ± 17.7
7. 7 ±2.1
9.9 ±2.4
2.0 ±0.6
2.6 ± 1.0
1.3 ±0.7
Cold
1.30±0.14
3000
88. 5 ±6.2
6.9 ± 1.7
2.7 ±0.6
1.0 ±0.4
1.2 ±0.5
0.9 ±0.5
a number of fry to reach the swim-up stage
CR = craniofacial defects, SK = skeletal defects, FF = finfold defects, ED = edema,
Rainbow Trout- 2000 data (Holm 2002)
CC
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i
-------
Rainbow Trout - 2000 data (Holm 2002)
100 -
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J5
Tl3
T3
O
60 -
O
-z.
^p 20 H
OH 0.5 1.0 15 2.0
[Se] in Muscles (|ig/g wet weight)
Holm Figure 2. Plot of percent normal (100 - percent total deformities) against selenium concentration in
adult rainbow trout muscle ww, 2000 data.
Rainbow Trout - 2001 data (Holm 2002)
100 -
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£ 80 -
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-------
Rainbow Trout - 2001 data (Holm 2002;
100 -
E
o
M—
(D
T3
80-
P3
(D 60
40
2 4 6 8 10 12
[Se] in Eggs (|ig/g wet weight)
Holm Figure 4. Plot of percent normal (100 - percent skeletal deformities) against selenium concentration
in rainbow trout eggs ww, 2001 data.
Rainbow Trout - 2001 data (Holm 2002)
03
E
100
CO
~ 80 H
80 -
c
CD
CJ
O
70 -
60 -
50
OOP
246 8 10
[Se] in Eggs (^.g/g wet weight)
Holm Figure 5. Plot of percent normal (100 - percent total deformities) against selenium concentration in
rainbow trout eggs ww, 2001data. EC20 value at 10.4 jig Se/g egg ww.
1-21
Draft November 12, 2004
-------
Brook Trout - 2000 and 2001
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6 8 10 12 14 16
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Egg Se Concentration
, wet weight)
Egg Se concentration
([j,g/g, wet weight)
Holm Figure 6. Plot of percent normal (100 - total abnormalities) for craniofacial, skeletal and finfold
deformities and edema against selenium concentration in brook trout eggs ww, 2000 and 2001 data.
1-22
Draft November 12, 2004
-------
The effect levels determined using the between streams or within streams approach resulted in values
based on ww in eggs or muscle. Several conversions were necessary to transform a selenium
concentration in egg ww to whole body dw. Using data reported by Holm et al., quantile regression was
used to estimate selenium in adult muscle (ww) from selenium in egg (ww) (see Projection of Muscle
Selenium Concentrations below). A percent moisture of 75.84% derived from rainbow trout data was
used to convert ww to dw and equation 1 was used to convert muscle dw to the whole body dw values
listed below (under Chronic Values).
Projection of Muscle Selenium Concentrations
Median concentrations of selenium in rainbowtrout muscles were projected from selenium concentrations
in rainbow trout eggs according to an empirical equation:
[Semuscle] = 0.1827 + 0.1287[Seegg]
(R = 0.6244, 5 df)
Parameters of the linear model were estimated by quantile regression, which minimizes the sum of
weighted absolute deviations. Such method is less sensitive to outliers than ordinary least squares
(Koenker and Portnoy 1996). This difference is clearly illustrated in Holm Figure 7: projections of
selenium concentrations in muscles of rainbow trout by the least squares regression line are consistently
greater than projections by the quantile regression line ([Semuscle] = 0.2613 + 0.1418[Seegg]) due to the
disproportional influence of one data point (6.6,1.9).
jz:
CS
"CD
CD
O)
1 D -
CO
CD
CO
DD
Projection of muscle [Se] (Holm 2002)
Leastsquares
Quantile regression
2 4 6 8 10
[Se] in eggs (|ig/g wet weight)
12
Holm Figure 7. Regression lines projecting selenium concentrations in muscles of rainbow trout as a
function of selenium concentrations in rainbowtrout eggs.
1-23
Draft November 12, 2004
-------
Chronic Values: Between streams approach
Rainbow trout 2000: effects (craniofacial, skeletal and finfold deformities and
edema) at 1.50 (ig Se/g muscle ww or 5.79 (ig Se/g dw whole body using
conversion fectors listed above; chronic value is 5.79 u£ Se/g dw whole body
Brook trout 2000: effects (craniofacial deformities) at 3.79 (ig Se/g muscle ww or
13.2 (ig Se/gdw whole body using conversion factors listed above; chronic value
is 13.2 ug Se/g dw whole body
Rainbow trout2001: no effects at 6.65 (ig Se/g eggww or 4.14(ig Se/g dw whole
body using conversion fectors listed above; chronic value is >4.14 \ig Se/g dw
whole body
Brook trout 2001: effects (finfold deformities) at 6.88 (ig Se/g eggww or 12.4 (ig
Se/g dw whole body using conversion factors listed above; chronic value is 12.4
\ig Se/g dw whole body
Within streams approach
Rainbow trout 2000: no value available; EC20 analysis not appropriate for data
sets
Brook trout 2000: no value available; EC20 analysis not appropriate for data sets
Rainbow trout 2001: EC20 value (craniofacial deformities) at 10.4 (ig Se/g egg ww
or 5.85 (ig Se/g whole body dw; chronic value is 5.85 ug Se/g whole body dw
Brook trout 2001: no value available; EC20 analysis not appropriate for data set
1-24 Draft November 12, 2004
-------
Kennedy, C.J., L.E. McDonald, R. Loveridge, M.M. Strosher. 2000. The effect of bioaccumulated
selenium on mortalities and deformities in the eggs, larvae, and fry of a wild population of cutthroat trout
(Oncorhynchus clarki lewisf). Arch. Environ. Contam. Toxicol. 39:46-52.
Test Organism:
Exposure Route:
Study Design:
Effects Data :
Cutthroat trout (Oncorhynchus clarki lewisi; spawning adults, 3-6 years)
dietary and waterborne - field exposure
Total selenium concentrations measured at the time the eggs were taken were
<0.1 (ig/L from the reference site and 13.3 to 14.5 (ig/L at the exposed site.
At reference and exposed site (Fording River, BC, Canada which receives
drainage from open-pit coal mining), eggs were stripped from females (n=20 from
reference site;n=17 from exposed site) and fertilized from milt from one male
collected at each site. Fertilized eggs were reared in well water and examined for
time to hatch, deformities (craniofacial, finfold, skeletal and yolk sac
malformations), and mortalities. Inspection of deformities in eggs were performed
using 40X magnification.
No significant correlations between the selenium concentrations in the eggs from
either site and: hatching time (reference, 25.5-26.5 days; exposed, 22-25.5 days);
percent deformities preponding (reference, 0-2.4%; exposed, 0-0.34%); percent
deformities after ponding (reference, 0-0.26%; exposed, 0-0.09%); percent
mortalities preponding (reference, 1.5-70.3%; exposed, 1-100%); percent
mortalities after ponding (reference, 0.34.3%; exposed, 1.5-43.7%); total percent
mortalities (reference, 2.8-55.8%; exposed, 3.7-100%). The average selenium
residue in tissues were as follows:
Site
reference
exposed
Adult fish liver,
(ig Se/g dw
8.2; Range: 3.4-14.6
36.6; Range: 18.3-1 14
Adult fish muscle,
(ig Se/g dw
2.4; 1.4-3.8
12.5; Range: 6.7-41
eggs,
(ig Se/g dw
4.6
21.2
Chronic Value:
Effects >12.5 (ig Se/g dwin muscle
>10.92 (ig Se/g dw estimated using the equation I to convert the selenium
concentration in muscle tissue (>12.5 (ig Se/g dw) of adult fish to a selenium
concentration in whole-body.
1-25
Draft November 12, 2004
-------
Hardy, R.W. 2002. Effects of dietary selenium on cutthroat trout (Oncorhynchus clarkf) growth and
reproductive performance. Annual report for Montgomery Watson Harza. April 30, 2002.
Test Organism:
Exposure Route:
Test Duration:
Study Design:
Effects Data :
Chronic Value:
Cutthroat trout (Oncorhynchus clarki, 0.9 g)
Dietary only
Six experimental dietary treatments were produced by cold extrusion. The
formulation of the diet was designed to be similar to commercial trout diets and
had a proximate composition of 45% protein and 16% lipid. Seleno-methionine
diluted in distilled water (100 ug/L) was added in appropriate volumes to each
batch of feed to facilitate pelleting. Measured dietary selenium concentrations
were 1.2 (control), 3.8, 6.4, 9.0,11.5, and 12 ug Se/g dw. Fry were fed initially at
a rate of 10 times per day 6 days a week to apparent saturation. Feeding
frequency decreased as fish grew.
124 weeks (865 days, 2.5 yrs)
Groups of 50 fish were placed into triplicate tanks (145 L) receiving 4-15 L/min
of hatchery water at 14.5°C and fed one of the six experimental diets. The fish in
each tank were bulk-weighed and counted every 14 days for the first 12 weeks of
the experiment, and then every 4 weeks until 48 weeks. Samples offish for
whole-body selenium analysis were taken at each sampling date for the first 12
weeks followed by every 3 months thereafter. After six months of feeding, the
fish were transferred to 575 L tanks and the number of replicate tanks per dietary
treatment was reduced to two. After 80 weeks of feeding, the fish were
transferred to 1050 L outdoor tanks each supplied with 70 L/min of constant
temperature (14.5°C) spring (hatchery) water. After 2.5 years of the feeding trial,
fish were spawned and whole body selenium level, egg selenium level, % eyed
eggs, % hatched eggs, and % deformed larvae were examined.
No signs of toxicity (reduced growth or survival relative to controls) were
observed in fish fed the highest dietary selenium treatment (12 ug Se/g dw) after
the first 80 weeks of exposure just prior to transfer outdoors. No signs of clinical
disease were evident, and no relationship was found between feed conversion
ratios and the level of selenium added to the feed. Whole body selenium levels
were approximately 6.8, 10, 12 and 12.5 ug Se/g dw in the four highest dietary
treatments. Nine months later, whole body selenium levels at spawning had
decreased somewhat to 5.21, 8.80, 9.37 and 6.66 ug Se/g dw in these four highest
dietary treatment groups, respectively. Percent survival from the eyed stage to
hatching varied among treatment groups, with the control having the highest
survival (97%) and the fifth dietary treatment group the second highest (93%).
Percent deformed larvae ranged from a low of 3.4% in controls to a high of 3 0%
in the 9.0 ug Se/g dw dietary treatment group; larvae in the two highest dietary
treatment groups only exhibited 7 and 6.8 %, respectively.
The chronic value for this study is aNOAEC of >9.37 ug Se/g dw whole-body
parent tissue based on embryo/larval deformity.
1-26
Draft November 12, 2004
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Bennett, William N., Arthur S. Brooks, and Martin E. Boraas. 1986. Selenium uptake and transfer in
an aquatic food chain and its effects on fathead minnow larvae. Arch. Environ. Contam. Toxicol. 15:513-
517.
Test Organism:
Exposure Route:
Test Duration:
Study Design:
Fathead minnow (Pimephales promelas; 2 to 8 day-old larvae).
Dietary only
Green alga, Chlorella pyrenoidosa were exposed to Se (H275SeO4) in culture
water for 3 days. Rotifers, Brachionus calyciflorus, were cultured in chambers
with selenium containing green algae at the ratio of 25 (ig algae/ml to 50 (ig
rotifer/ml for 5 hr. The rotifers were filtered to separate them from the algae and
immediately heat-killed. The Se concentration in the rotifers was measured for
75 Se activity.
9 to 30 days
Selenium uptake by larval fathead minnows was measured in three experiments.
Se-contaminated and control rotifers for feeding to larval fish were prepared in
advance using the low algae:rotifer ratio. Daily equal volumes of rotifers weie
divided among five 800 mL polypropylene larval chambers. Three chambers
received Se-contaminatedrotifers and two received control rotifers. The rotifers
were dead at the time of feeding (heat killed).
Larval fish were hatched from eggs spawned in the laboratory. After hatching,
active larvae were divided equally among the larval test chambers (daily renewal
exposures using declorinated Lake Michigan water). Larvae were initially fed
rotifers raised on control algae (no selenium). The age of the larvae when first
fed Se-contaminated rotifers was 4, 9, and 3 days post-hatch for experiments 1, 2,
and 3, respectively. Larval fish were fed Se-contaminated rotifers for 7, 9, and 7
days in the 3 experiments. A post-exposure observation period of 19 and 2 days
was used for experiments 1 and 2, respectively. During this time the larvae were
fed control rotifers. Daily, larvae from a replicate were removed from the test
chamber, washed, placed in a 20 ml vial, and counted for 75Se activity for 20 min.
All larvae were then placed in test chambers with fresh food rations. At the end
of the study all fish were individually dried and weighed.
1-27
Draft November 12, 2004
-------
Initial feeding of control diet
(days)
Day Se diet first fed
Day Se diet last fed
Observation days on control diet
Age at study termination (days)
Experiment 1
3
4
11
19
30
Experiment 2
8
9
17
2
19
Experiment 3
2
3
9
0
9
Effects Data:
Mean food Se concentration (|ig/g)
Food intake (|ig rotifers/larva)
Initial larvae mean dry wt. at start
of Se-laden food (|ig)
Final larvae mean dry wt. (|ig) at
end of test
Final mean larval Se content (|ig
Se/larva)b
Final mean larval Se
concentrations (|ig Se/g dw)
Experiment 1
>70
50
90
1470 (Control)
800 (Treatment)8
0.0062
43.0
Experiment 2
68
1330
400
1888 (Control)
1354 (Treatment)3
0.0700
51.7
Experiment 3
55
1190
100
475 (Control)
416 (Treatment)
0.0248
61.1
a Significantly different from the control.
b Values when Se-ladea feeding was ended.
Chronic Value:
Selenium was measured in the test water during the feeding exposures, but the
concentrations were insignificant (0.84 (ig/L). Survival was not affected by the
selenium exposures. Preliminary tests showed that fathead minnow larvae would
reach plateau concentrations of selenium within the 7- to 9-day exposure periods.
The food supply was sufficient to sustain growth of the larvae during the study,
according to the authors. The authors state that selenium uptake and higher
selenium content in experiment 2 larvae was due to their larger size and ability to
consume more rotifers/unit time. Se-exposed larvae were significantly smaller
(p<0.05) in mass than controls for experiments 1 and 2.
The estimated whole-body chronic value for this study, determined as the
geometric mean of the final mean larval selenium concentrations measured in the
three experiments, i.e., 43.0, 51.7, and 61.1 (ig/g dw, respectively, is 51.40 (ig
Se/g dw.
1-28
Draft November 12, 2004
-------
Ogle, R.S. and A.W. Knight. 1989. Effects of elevated foodborne selenium on growth and reproduction
of the fathead minnow (Pimephales promelas). Arch. Environ. Contam. Toxicol. 18:795-803.
Test Organism:
Exposure Route:
Test Treatments:
Test Duration:
Study Design:
Effects Data:
Fathead minnows (Pimephalespromelas; juvenile, 59 to 61 d old)
Dietary only
Purified diet mix spiked with inorganic and organic selenium: 25 percent selenate,
50 percent selenite, and 25 percent seleno-L-methionine, homogenized in dextrin.
Completely randomized block design (2 blocks); 4 replicates per block (n = 8
replicates total per treatment). Actual mean total selenium levels in each
exposure treatment were: 0.4 (control), 5.2, 10.2, 15.2, 20.3, and 29.5 (ig/g dw.
Fish used in the first randomized block (F2 generation fish) were progeny from F{
generation originally obtained from the Columbia National Fishery Research
Laboratory, some of which were used in an initial range-finding experiment. Fish
obtained from a commercial supplier were used in the second randomized block.
The prepared diet was extruded into 1.5 mm pellets which were air-blow dried to
5 percent moisture content and crushed and sieved so that only particles retained
by an 11.8 mesh/cm sieve were used in the study. The amount of selenium in
water that leached from the food during the experiment averaged only 0.8 (ig/L.
105 days, F2 generation (block one) and commercial fish (blocktwo);
14 days F3 generation
Ten fish were randomly placed in each cell per block (n = 8x10, or 80 fish total
per treatment). Fish were fed twice daily at 6 percent body weight per day, with
wastes and uneaten food removed 30 min. after each feeding. Test tanks were
flushed with two tank volumes of fresh test water after each feeding (solution
renewal). Growth (as wet weight) was determined every two weeks by bulk
weighing, and one fish from two of the cells per treatment in a given block (n = 4
total per treatment) was removed for selenium (whole-body) analysis. After 105
days of exposure, a single male and female fish from each treatment replicate (n =
4 breeding pairs per treatment in a given block, or 8 breeding pairs per treatment
total) were placed in 250 ml beakers and inspected for spawning activity for 30
days following the first spawning event for that pair (each pair being one
replicate). Gonads and muscle tissue were dissected for selenium analysis from
these fish at the end of the 30 days spawning period. The spawning substrates
were inspected daily for eggs to determine fertility and viability. Samples of not
more than 50 eggs from each spawn were incubated in flowing, aerated water and
inspected for percent hatch determination. Ten larvae from each incubated brood
were transferred to separate glass test chambers and maintained (48 h renewal;
fed brine shrimp twice daily) for 14 days to determine percent larval survival.
There was no effect of selenium on any of the reproductive parameters measured
at the dietary concentrations tested. Percent hatch and percent larval survival
were very high (>87.4 percent) and essentially equal for all of the treatments.
1-29
Draft November 12, 2004
-------
Growth of pre-spawning adults was affected by the selenium exposure. Growth
data are given in the following table:
Effects on Fathead Minnow Growth after 98 days of Exposure to Dietary Selenium
Measured mean selenium in
diet, (ig/g dw
0.4
5.2
10.2
15.2
20.3
29.5
Whole-body selenium,
Mg/g dw
1.76
2.78
3.42
5.40
6.58
7.46
Mean fish weight,
g ww
1.30
1.24
1.20
1.21
1.09
0.94
Chronic Value:
An EC20 value could not be calculated for these data because the data did not
meet the minimum requirements for analysis. The MATC for growth of pre-
spawning fathead minnows versus levels of selenium found in whole-body tissue
was the GM of 5.40 and 6.58 (ig/g dw, or 5.961 (ig Se/g dw.
1-30
Draft November 12, 2004
-------
Schultz, R. and R. Hermanutz. 1990. Transfer of toxic concentrations of selenium from parentto
progeny in the fathead minnow (Pimephalespromelas). Bull. Environ. Contam. Toxicol. 45:568-573.
Test Organism:
Exposure Route:
Study Design:
Effects Data :
Fathead minnow (Pimephales promelas; Adults)
Dietary and waterborne
Selenite was added to artificial streams which entered the food web; thus, fish
were also exposed to selenium in the diet.
Four Monticello artificial streams were used for the study which lasted from
September 1987 to September 1988. For each study, two streams (treated) were
dosed continuously to achieve 10 (jg/L and two streams served as controls. Mean
selenium concentrations at the head of the treated streams were 9.8 ±1.2 and 10.3
±1.7 (ig/L, respectively. The concentrations of selenium measured in the water
from controls streams were all less than the detection limit, i.e., 2 (ig/L.
Spawning platforms were submerged into each stream. One subset of six embryo
samples (n = 2000 embryos per sample) were collected from the streams for
selenium analysis. Another subset often embryo samples were reared in
incubation cups receiving the same streamwater dosed with sodium selenite via a
proportional diluter. The treated embryos in egg cups received an average 9.7 ±
2.6 (ig of selenium/L. Samples of hatched larvae were analyzed for selenium
content while others were inspected for occurrence of edema and lordosis. Prior
to test termination, female parents were seined. The mean selenium content in the
ovaries of seven to eight females from the treated and control streams was
reported.
Edema and lordosis occurred in approximately 25 percent of the fish spawned and
reared in 10 (ig of selenium/L. Corresponding occurrence in control fish
incubated in the egg cups was only 1 and 6 percent, respectively. Selenium
residues in the ovaries of females from the control and treated streams were 0.77
and 5.89 (ig/g ww. Assuming 85 percent moisture content in the ovaries (see
Gillespie and Baumann below), these concentrations equate to 5.133 and 39.27 (jg
Se/g dw.
Chronic Value:
<18.21 (ig Se/g dw estimated using equation II to convert the selenium
concentration in adult female ovaries (3927 (ig Se/g dw) to a selenium
concentration in whole-body.
1-31
Draft November 12, 2004
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Beyers, D.W. and Sodergren, C. 2001a. Evaluation of interspecific sensitivity to selenium exposure:
Larval razorback sucker versus flannelmouth sucker. Larval Fish Laboratory. Department of Fishery and
Wildlife Biology, Colorado State University, Fort Collins, Colorado.
Test Organism:
Exposure Route:
Study Design:
Effects Data :
Chronic Value:
Larval flannelmouth sucker (Catostomus latipinnis) and larval razorback sucker
(Xyrauchen texanus)
Dietary and waterborne - laboratory exposure (28-d early life stage)
Continuous flow diluter supplied a range of aqueous test concentrations <1, 25.4,
50.6, 98.9, and 190.6 (ig/Lselenate. Well water was used as the dilution water.
Across the range of aqueous exposure concentrations, each test chamber was fed
the same daily ration of living rotifers containing selenium at <0.702, 1.35, 2.02,
4.63, and 8.24 (ig/g dw, respectively. Rotifers accumulated selenium from algae
(Chlorella vulgzris) exposed to 0, 25, 50, 100, and 200 (ig/L selenate.
Replicated (n=4) exposure beakers using a randomized, balanced 5x2 factorial
design (1st factor - selenium; 2nd factor - species). Survival was monitored daily
and growth measured at the end of the 28-day exposure. Selenium was measured
in the larvae at the end of the 28-day exposure.
No survival effects were observed and there were no decreases in fish weight or
length. Fish mass was found to increase as a function of selenium concentration.
The chronic values for the flannelmouth sucker and razorback sucker were >10.2
and >12.9 (ig Se/g dw, respectively, based on the concentrations of selenium
measured in whole-body tissue of larval fish at the highest water and dietary
selenium concentrations.
1-32
Draft November 12, 2004
-------
Beyers, D.W. and Sodergren, C. 2001b. Assessment of exposure of larval razorback sucker to selenium
in natural waters and evaluation of laboratory-based predictions. Larval Fish Laboratory. Department of
Fishery and Wildlife Biology, Colorado State University, Fort Collins, Colorado.
Test Organism:
Exposure Route:
Study Design:
Effects Data :
Chronic Value:
Larval razorback sucker (Xyrauchen texanus)
Dietary and waterborne - laboratory exposure (28-d early life stage)
Larvae were exposed in a daily static-renewal system to control water
(reconstituted very hard) and site waters: De Beque, Orchard Mesa, North Pond
diluted 50%, and North Pond. Each water type received either a control diet
(rotifers) or a diet previously exposed to the site water (site food: rotifers fed
algae exposed to respective site water).
Replicated (n=4) exposure beakers using a randomized, balanced 5x2 factorial
design (1st factor - test water type; 2nd factor - rotifers cultured in control water or
in site water). Survival was monitored daily and growth measured at the end of
the 28-day exposure. Selenium was measured in the larvae at the end of the 28-
day exposure.
No survival effects were observed. There were no significant decreases in growth
offish exposed to both site water and site food compared to fish exposed to
control water and control food. There was a significant increase in growth offish
exposed to site water and control food relative to fish exposed to control water
and control food (p<0.0001). There were reductions in the growth offish (14%)
exposed to site water and site food compared to site water and control food
(p<0.0001). Due to the lack of a dose-response relationship in both the
concentration of selenium in the food (rotifers) and growth, and the concentration
of selenium in the fish larvae and growth, the authors did not attribute the effect
of site food on the growth offish to selenium.
The NOAEC for the razorback sucker larvae in the four site water types based on
selenium in whole-body tissue were: De Beque >5.45 (ig Se/g dw; Orchard Mesa
>11 (ig Se/g dw; North Pond 50% dilution >41.1 (ig Se/g dw; North Pond >42 (ig
Se/g dw. Because no significant effects were observed in larvae exposed to North
Pond water at >42 (ig Se/g dw whole-body tissue, this value was selected as the
chronic value for the study.
1-33
Draft November 12, 2004
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Bryson, W.T., W.R.Garrett, M.A. Mallin, K.A. MacPherson, W.E. Partin, and SE. Woock. 1984.
Roxboro Steam Electric Plant 1982 Environmental Monitoring Studies, Volume n, Hyco Reservoir
Bioassay Studies. Environmental Technology Section. Carolina Power & Light Company.
28-day Embryo/Larval Study
Test Organism: Bluegill sunfish (Lepomis macrochirus; embryos and larvae)
Exposure Route:
Study Design:
Effects Data
Chronic Value:
dietary and waterborne - field exposure
Native adult bluegill were collected from Hyco Reservoir in Person County,
North Carolina and from a nearby control lake (Roxboro City Lake). Hyco
Reservoir is a cooling lake for Carolina Power & Light and receives the discharge
from the ash storage pond. No selenium values were given for Hyco Reservoir,
total selenium was not detected in the control lake (< 1 (ig/L). A mean selenium
for the ash pond effluent from a previous study was 53 (ig/L (N=59; range 35-80
All combinations of crosses between the Hyco and control fish were made using
gametes from the collected fish. Fertilized eggs were exposed in egg cups to 0,
20 and 50 percent ash pond effluent under flow-through conditions. Percent
hatch and swim-up success were measured. Swim-up larvae were released to
exposure tanks where there were fed zooplankton collected from Hyco and the
control lake. Larvae were observed for 28 days at which time survival and weight
were measured.
Survival to the swim-up stage was different between larvae from Hyco females
fertilized with either male type and those larvae from control females fertilized
with either male type. All crosses involving a Hyco female resulted in larvae
exhibiting 100 percent mortality prior to reaching swim -up. Percent survival from
hatch to 28 days for larvae from control females exposed to control water and fed
control lake zooplankton was only 5 and 12 percent for the two replicates so no
meaningful comparisons can be made to the different dilution exposures or diet
exposure. The mean concentrations of selenium in the ovaries, female liver and
female muscle were 49, 130, and 84 (ig/g dw, respectively.
Effect level: < 49, <130 and < 84 (ig Se/g dw in adult ovaries, liver and muscle,
respectively
<59.92 (ig Se/g dw estimated using the equation I to convert the selenium
concentration in the muscle of Hyco females (84 (ig Se/g dw) to a selenium
concentration in whole-body.
1-34
Draft November 12, 2004
-------
Ingestion Study
Test Organism:
Exposure Route:
Study Design:
Effects Data:
Chronic Value:
Bluegill sunfish (Lepomis macrochirus; 30-day old larvae)
Dietary and waterborne - field exposed adults
Juvenile bluegill from crosses with females in 0, 20 and 50 percent ash pond
effluent were transferred to control water and fed zooplankton from either Hyco
or the control lake. Selenium in Hyco and control zooplankton was 45 and 1.9
(ig/g dw, respectively. Duration was not given.
Survival and observations on pathology and morphology were made in the two
diet treatments.
Mortality in larvae fed control zooplankton was 23.7percent, whereas mortality
in larvae fed Hyco zooplankton was 97.3 percent. There were no differences in
survival (for two diet treatments) in larvae that were raised for the 30 days prior
to the test in different effluent concentrations (0, 20 50 percent). The average
selenium concentrations in the larvae fed control and Hyco zooplankton were 1.9
and 24.7 (ig/g dw, respectively.
Effect level for larval survival: <24.7 (ig Se/g dw in larvae
None recommended for larval tissue.
1-35
Draft November 12, 2004
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Bryson, W.T., W.R.Garrett, M.A. Mallin, K.A. MacPherson, W.E. Partin, and SE. Woock. 1985a.
Roxboro Steam Electric Plant Hyco Reservoir 1983 Bioassay Report. Environmental Services Section.
Carolina Power & Light Company. September 1985.
28-day Embryo/Larval Study
Test Organism:
Exposure Route:
Study Design:
Effects Data :
Bluegill sunfish (Lepomis macrochirus; embryos and larvae)
dietary and waterborne - field exposed
Resident adult bluegill were collected from Hyco Reservoir in Person County,
North Carolina and from a nearby control lake (Roxboro City Lake). Hyco
Reservoir is a cooling lake for Carolina Power & Light and receives the discharge
from the ash storage pond. For embryo/larval study up to swim-up stage, control
fish were collected from the unaffected portion of Hyco.
Repeat of 1982 28-day Embryo/Larval Study. Three crosses between: Hyco
female and Hyco male; control female with Hyco male; and control female with
control male. Gametes were fertilized and maintained for the 28-day test in ash
pond effluent dilutions of 0, 20 and 50 percent. Percent hatch, percent swim-up
success and survival were measured to 28 days post hatch. Two treatments were
replicated and fed zooplankton collected from Hyco-affected and Hyco-
unaffected (control). Larvae were observed for 28 days at which time survival
and weight were measured.
Embryo/Larval Study up to Swim-up Stage. Five crosses were made between fish
collected from the affected and unaffected areas. Percent hatch, percent swim-up
and survival were measured until swim-up (approximately 34 days after hatch).
28-day Embryo/Larval Study. All larvae that hatched from eggs obtained from
Hyco females died prior to completing swim-up (see table below).
Effect level (larval survival): < 30, < 33 and < 59 (ig Se/g dw for adult female
bluegill in ovaries, liver and muscle, respectively
1-36
Draft November 12, 2004
-------
Summary of 28-day embryo larval study
% effluent
0
20
20
50
0
20
50
0
20
20
50
parent
source in
cross
MXF
HXH
HXH
HXH
HXH
HXC
HXC
HXC
CXC
CXC
CXC
CXC
% hatch
92
98
92
97
89
96
60
79
90
88
72
% swim-
up
0
0
0
0
87
96
84
95
96
97
92
%
survival,
28-days
0
0
0
0
18
34
58
40
36
25
42
adult tissue, (ig Se/g dw
gonad
M
33
33
33
33
33
33
33
nd
nd
nd
nd
F
30
30
30
30
2.2
2.2
2.2
2.2
2.2
2.2
2.2
liver
M
43
43
43
43
43
43
43
37
37
37
37
F
33
33
33
33
4.4
4.4
4.4
4.4
4.4
4.4
4.4
muscle
M
62
62
62
62
62
62
62
27
27
27
27
F
59
59
59
59
2.7
2.7
2.7
2.7
2.7
2.7
2.7
Chronic Value:
<43.70 (ig Se/g dw estimated using equation I to convert the selenium
concentration in the muscle of Hyco females (59 (ig Se/g dw) to a selenium
concentration in whole-body.
Embryo/larval study to swim-up. Percent swim-up of larvae from parents
collected in non-affected Hyco averaged 93 percent, whereas percent swim-up
from larvae collected from affected Hyco was 12 percent. Effect levels were
determined for adult female and larval tissues. Larval tissues were averaged
across effluent concentrations (geometric mean).
Effect level (percent swim-up):
Adult female ovaries: >9.1 (ig/g dw; <30 (ig/g dw
Adult female liver: >26 (ig/g dw, <33 (ig/g dw
Adult female muscle: >25 (ig/g dw, <59 (ig/g dw
Larvae: >12.8 (ig/g dw; < 165 (ig/g dw
1-37
Draft November 12, 2004
-------
Summary of Embyo/Larval Study up to Swim -up - Affected vs Unaffected Hyco
date of
fert.
6-24
6-27
6-28
6-28
6-29
7-14
7-26
7-27
Parents'
capture
location in
Hyco
affected
affected
affected
affected
affected
unaffected
unaffected
unaffected
percent hatch
at % effluent
0
93
99
29
98
88
92
99
76
20
98
88
34
86
93
80
94
84
50
94
77
35
91
85
84
93
86
percent swim-up
at % effluent
0
0
0
25
5
59
79
100
100
20
0
0
14
0
42
92
98
89
50
0
0
3
0
25
89
98
91
selenium in tissue, (ig/g dw
adult female
ovary
30
30
30
30
30
9.1
9.1
9.1
liver
33
33
33
33
33
26
26
26
muse
59
59
59
59
59
25
25
25
larvae
0: 130
20: 120
0: 130
20: 120
0: 130
20: 120
0: 130
20: 120
0: 130
20: 120
0: 19
20: 11
50: 10
0: 19
20: 11
50: 10
0: 19
20: 11
50: 10
Chronic Value:
The chronic value estimated for the percentage larvae reaching the swim-up stage
is presented as a range >25 (ig Se/g dw in muscle tissue of Hyco females from the
unaffacted area and >59 (ig Se/g dw in muscle tissue of Hyco females from the
affected area. Using equation I to convert the selenium concentration in the
muscle of Hyco females to a selenium concentration in whole-body these values
become >20.29 (ig Se/g dw and <43.70 (ig Se/g dw, respectively.
1-38
Draft November 12, 2004
-------
Bryson, W.T., K.A. MacPherson, M.A. Mallin, W.E. Partin, and S.E. Woock. 1985b. Roxboro Steam
Electric PlantHyco Reservoir 1984 Bioassay Report. Environmental Services Section. Carolina Power &
Light Company
Ingestion Study
Test Organism:
Exposure Route:
Test Treatments:
Test Duration:
Study Design:
Effects Data:
Chronic Value:
Bluegill sunfish (Lepomis macrochirus; juvenile- hatchery raised)
Dietary only
5 diets: Se form (nominal selenium concentration in base diet)
seleno-DL-cystine (5 (ig/g)
seleno-DL-cystine (10 (ig/g)
seleno-DL-methionine (5 (ig/g)
sodium selenite (5 (ig/g)
Hyco zooplankton (5 (ig/g)
60 days
Each treatment contained 40 fish which we re maintained in a flow-through
system. Fish were fed at 3 percent of their body weight. Length and weight were
measured on days 30 and 60. Total selenium was measured in liver and whole-
body.
No decreased length or weight in any of the Se-diets relative to the control.
all values are whole-body
seleno-DL-cysteine: >2.16 (ig Se/g dw
seleno-DL-cysteine-2X: >3.74 (ig Se/g dw
seleno-DL-methionine: >2.46 (ig Se/g dw
sodium selenite : >1.21 (ig Se/gdw
Hyco zooplankton: >2.35 (ig Se/g dw
Because none of the selenium-spiked diet formulations affected growth of
juvenile fish at the concentrations tested, the chronic value selected for this study
is >3.74 (ig Se/g dw for the seleno-DL-cysteine-2X formulation.
Source and Exposure Embryo-Larval Study
Test Organism: Bluegill sunfish (Lepomis macrochirus; Adults from Hyco and a control lake)
Exposure Route: dietary and waterborne - field exposure
Test Treatments:
Four treatments:
Hyco-collected fish exposed to Hyco water in flow through spawning tanks.
Hyco-collected fish in control water in flow through spawning tanks.
1-39
Draft November 12, 2004
-------
Test Duration:
Study Design:
Effects Data:
Control fish exposed to Hyco water in flow through spawning tanks.
Hyco-collected fish in control water in flow through spawning tanks.
Adult fish were in spawning tanks 4-7 months
Eggs from each treatment were observed for percent hatch and percent swim-up.
Fish collected from the control lake did not spawn. Percent hatch and percent
swim-up from Hyco fish in Hyco and control water are given in the table below.
The percent hatch and percent swim-up were >83 and >83 for all the Hyco fish
suggesting no effect for these endpoints.
Source of
parents
Hyco
Hyco
Control
Control
Se in parental
liver tissue,
Mg/g dw
18.6
18.6
13.8
13.8
water type for
eggs and
larvae
Hyco
well water
Hyco
well water
N
16
10
a
12
percent hatch
86.6
83.8
a
86.0
percent swim-
up
91.1
95.5
83.3
97.4
percent hatch unknown.
Chronic Value:
The chronic value for this study is >18.6 (ig Se/g dw liver tissue, or >5.45 (ig of
Se/g dw whole body tissue using equation III.
1-40
Draft November 12, 2004
-------
Gillespie, R.B. and P.C. Baumann. 1986. Effects of high tissue concentrations of selenium on
reproduction by bluegills. Trans. Am. Fish. Soc. 115:208-213.
Test Organism:
Exposure Route:
Test Treatments:
Study Design:
Effects Data:
Bluegill sunfish, wild-caught (Lepomis macrochirus; adults; embryos and larvae)
dietary and waterborne - field exposure
High selenium adult fish were collected (electrofishing and with Fyke nets) from
Hyco Reservoir. Low selenium adult fish were collected from Roxboro City
Lake, Roxboro, NC.
All possible combinations of bluegill parents from Hyco Reservoir and Roxboro
City Lake were artificially crossed in June and July, 1982 and 1983, respectively.
Fertilization success was assessed by stripping subsamples of 100 to 500 eggs per
female and combining 1hem with 2 ml of sperm. All zygotes were reared in
Roxboro City Lake water and percent fertilization was estimated 2-3 hours later
as the proportion of mitotically active zygotes. To estimate hatching success,
gametes were combined as before and subsamples of 100 to 300 embryos per
cross were transferred to egg cups and maintained in closed aquaria receiving
recirculated Roxboro City Lake water. Percent hatch (approx. 2d at 22 to 25°C)
was based on the number of yolk-sac larvae.
In 1982, about 200 embryos from 8 crosses were observed and preserved at
intervals up to 40 h afer fertilization, and about 450 larvae were preserved at
intervals of 40 to 180 h after fertilization. In 1983, about 1,800 larvae were
observed and preserved from 40 to 150 hr from crosses involving females from
Hyco Reservoir, and about 40-300 hrfor crosses involving females from Roxboro
City Lake (10 crosses total).
No significant differences were found in percent fertilization or in percent hatch
among parent combinations from the 18 crosses made in June 1982 and July
1983. In contrast, larvae from all crosses involving a Hyco female were
edematous; 100 percent of the larvae were abnormal in 7 of 8 crosses. Note: This
outcome was observed when the same female from Hyco Reservoir was crossed
with males from either Hyco Reservoir or Roxboro City Lake. The range of
selenium concentrations in the ovaries of Hyco Reservoir females used for the
cross experiments was from 5.79 to 8.00 (GM = 6.945 (ig/g wet weight; n=7).
The reported concentrations of selenium in ovaries and carcasses of females
collected from Hyco Reservoir in 1982 and 1983 were 6.96 and 5.91 (ig/g wet
weight (n=22 and 28, respectively). The reported concentrations of selenium in
ovaries and carcasses of females collected from Roxboro City Lake in 1982 and
1983 were 0.66 and 0.37 (ig/g wet weight (n=14 and 19, respectively). The mean
selenium concentration in bluegill larvae (n=222) from artificial crosses of
parents from Hyco Reservoir was 28.20 (ig Se/g dw.
1-41
Draft November 12, 2004
-------
Chronic Value: <21.47 (ig Se/g dw estimated using equation II to convert the selenium
concentration in ovaries of Hyco females (46.30 (ig Se/g dw; assuming 85 percent
moisture content) to a selenium concentration in whole-body.
1-42 Draft November 12, 2004
-------
Coyle, J.J.,D.R. Buckler and C.G. Ingersoll. 1993. Effect of dietary selenium on the reproductive
success of bluegills (Lepomis macrochirus). Environ. Toxicol. Chem. 12:551-565.
Test Organism:
Exposure Route:
Bluegill sunfish (Lepomis macrochirus; two-year old pond-reared adult fish and
resultant fry)
Dietary and waterborne
Seleno-L-methionine added in an aqueous solution to Oregon moist pellets;
moisture content of diet was 25 percent.
Waterborne
Flow through, 10 (ig Se/L nominal, 6:1 ratio of selenate:selenite, 98 percent
purity, adjusted to pH 2 with HC1 to prevent bacterial growth and change in
oxidation states of Se(IV) and Se(VI).
Test Duration: 140 days
Study Design: The experiment consisted of a test control and food control (see Test Treatment
table below) with fish (n=28 initially) in the four remaining treatments fed one of
the four seleno-methionine diets in combination with 10 (ig Se/L in water.
Spawning frequency, fecundity, and percentage hatch were monitored during the
last 80 days of the exposure period. Survival of resulting fry (n=20)was
monitored for 30 days after hatch. Adults and fry were exposed in separate,
modified proportional flow-through diluters. Fry were exposed to the same
waterborne selenium concentrations as their parents. Adults were fed twice daily
ad libitum. Whole-body selenium concentrations in adult fish were measured at
days 0, 60, and were calculated from individually analyzed carcass and gonadal
tissue (ovaries and testes) at day 140. Eggs not used in percentage of hatch
determinations were frozen and analyzed for total selenium.
Measured Se in:
water
(^ Se/L)
diet
(|ig Se/g dw)
Test Treatments
1
(test control)
0.56
0.76
2
(food control)
8.4
0.76
3
10.5
4.63
4
10.5
8.45
5
10.1
16.8
6
11.0
33.3
Effects Data:
There was no effect of the combination of highest dietary selenium concentration
(33.3 (ig/g dw) in conjunction with exposure to a waterborne selenium
concentration of 11.0 (ig/L on adult growth (length and weight), condition factor,
gonad weight, gonadal somatic index, or reproductive endpoints (i.e., spawning
frequency, number of eggs per spawn, percentage hatch) during the 140-day
exposure. The mean corresponding whole-body selenium concentration in adults
1-43
Draft November 12, 2004
-------
exposed to this waterborne and dietary selenium combination was 19 (ig/g dw.
Survival of fry from the exposed adults was affected by 5 days post-hatch.
Concentrations of whole-body selenium in adult tissue at day 60 were used to
determine effects in the fry because eggs were taken for the larval tests beginning
at day 60 of the adult exposure.
Effects on Adults
Se in diet,
Mg/g dw
0.8
0.8
4.6
8.4
16.8
33.3
Se in water,
Mg/L
0.5
7.9
10.5
10.5
10.1
10.1
whole-body
Se (140 d),
Mg/g dw
0.8
1.0
3.4
6.0
10
19
replicate
A
B
A
B
A
B
A
B
A
B
A
B
total no.
spawns
15
10
12
11
20
12
2
9
13
13
14
4
eggs/spawn
14,099
5,961
9,267
9,255
9,782
13,032
10,614
7,995
10,797
9,147
8,850
8,850
hatchability,
%
94.5
90.5
89.5
84.5
86.5
96.5
96.5
90
83
91.5
80
80
1-44
Draft November 12, 2004
-------
Effects on Larvae
Se in diet, (ig/g dw
0.8
0.8
4.6
8.4
16.8
33.3
Se in water, (jg/L
0.5
7.9
10.5
10.5
10.1
10.1
adult whole -body
(60 d), ng/g dw
0.9
0.9
2.9
4.9
7.2
16
mean survival, %
92
93
90
95
87
7
Chronic Value:
The EC20 value calculated for survival of fry versus levels of selenium found in
the eggs and whole-body tissue of adults after 60 dof exposure is 8.954 (ig Se/g
dw.
1-45
Draft November 12, 2004
-------
1,0
C 0-8-
g
tf
o
Q.
O 0.6
3
c/)
0.4
0.2-
0.0
Bluegill (Coyle 1993)
910 2 3 4567810.0
Whole body Se[^g/g dw]
1-46
Draft November 12, 2004
-------
Cleveland, L. et al. 1993. Toxicity and bioaccumulation ofwaterborne and dietary selenium in juvenile
bluegill sunfish (Lepomis macrochirus). Aquatic Toxicol. 27:265-280.
Test Organism:
Life Stage:
Exposure Route:
Study Design:
Effects Data :
Bluegill sunfish (Lepomis macrochirus)
juvenile (5 months - waterborne exposure; 3 months - dietary exposure)
waterborne (60-d) and dietary (90-d) - separate exposures
waterborne - 6:1 selenate:selenite at 0.17, 0.34, 0.68, 1.38, 2.73 mg/L; dietary -
seleno-L-methionine in Oregon moist at 1.63, 3.25, 6.5, 13, 26 (ig Se/g dw)
Fish were exposed using a flow-through diluter. Each test consisted of an
exposure and a depuration phase. Whole body tissue measurements were made at
31 and 60 days ofwaterborne exposure and at 31, 59 and 90 days of dietary
exposure. Mortality and condition factor, K (weight x 105/length3), were
measured at selected intervals.
The waterborne exposure (see table below) was determined to have an EC20 =
4.07 (ig Se/gdw (1.96-8.44 (ig/g95% CL). However, because it was awater-only
exposure, it was not considered in the derivation of the FCV.
A mortality effect level for the dietary exposure could not be calculated because
the highest selenium whole body concentration (13.4 (ig Se/g dw) only had 17.5%
mortality. The middle selenium concentration did have 22.5% mortality.
Cleveland et al. reported a significant decrease in K between 4.7 and 7.7 (ig/g dw
(see table below).
Waterborne Exposure Study
measured selenium in
water ((ig/L)
20 (control)
160
330
640
1120
2800
60-d measured
selenium in whole body
((ig/g dw)
1.1
2.8
4
5.3
9.8
14.7*
60-d mortality (%)
10
12.5
22.5
52.5
70
97.5
condition factor (K)
1.5
1.5
1.6
1.5
1.6
NA
*A 30-d measurement because all fish were dead at 60 days in this concentration.
Dietary Exposure Study
measured selenium in
food ((ig/g ww)
60-d measured
selenium in whole body
((ig/g dw)
60-d mortality (%
condition factor (K)
1-47
Draft November 12, 2004
-------
0.68 (control)
2.3
3.5
6.6
12.7
25
1
2.1
3.3
4.7
7.7
13.4
5
7.5
10
22.5
15
17.5
1.3
1.3
1.3
1.3
1.2
1.2
Chronic Value:
Given the very slight reduction in K (1.3 to 1.2) and the uncertain relevance of
growth data, the NOAEC is interpreted to be 13.4 (ig Se/g dw for this study; and
the chronic value is >13.4 (ig Se/g dw.
1-48
Draft November 12, 2004
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Lemly, A.D. 1993a. Metabolic stress during winter increases the toxicity of selenium to fish. Aquatic
Toxicol. 27:133-158.
Test Organism:
Exposure Route:
Test Duration:
Study Design:
Effects Data
Chronic Value:
Bluegill sunfish (Lepomis macrochirus; juvenile 50-70 mm)
Waterborne and dietary
Water
1:1 selenite:selenate in stock at pH 2; metered in to reach 5 (ig/L
Diet
seleno-L-methionine in TetraMin (5 (ig/g dw)
180 days
Fish were exposed (treatment and control) under intermittent flow-through
conditions for 180 days. Tests were run at 4° and 20°C with biological
(histological, hematological, metabolic and survival) and selenium measurements
made at 0, 60, 120 and 180days. Fish were fed at a rate of 3% body weight per
day. All treatments were initiated at 20°C and then decreased in the cold
treatment at a rate of 2°C per week for 8 weeks to reach 4°C and then maintained
at that temperature for the remainder of the 180 days.
In the 20°C test, fish accumulated 6 (ig/g dw selenium (whole-body) with no
significant effect on survival (4.3% and 7.4% mortality in control and treatment,
respectively). In the 4°C test, fish exposed to selenium accumulated 7.9 (ig/g dw
(whole-body) selenium and had significant mortality after 120 (33.6%) and 180
days (40.4%) relative to control (3.9%). Several hematological measurements
were significantly different in both the warm and cold selenium exposures
relative to controls. Both warm and cold selenium treatments also had greater O2
consumption than controls. Fish lipid content in the cold Se treatment decreased
more than the cold control; lipid content did not decrease in either the warm
control or the warm Se treatment (see summary tables below). The results
suggest significant mortality occurs in juvenile bluegill during winter months
when tissue concentrations reach 7.91 (ig/gdw and lipid levels decrease to 6
percent.
20°C, > 6 (ig/g Se whole-body; 4°C, < 7.91 (ig/g dw Se whole body
1-49
Draft November 12, 2004
-------
Mean Concentration of Selenium in Tissues, Cumulative Survival*, Percent Lipid Content and Oxygen Consum
day
0
60
120
180
cold - Se control
Sea
1
1
1.1
1.4
Surv.
%
100
97.1
97.1
97.1
lipid,
%
13.2
12.5
11.5
10.5
02b
98
58
57
57
cold + Se
Sea
1
5.8
7.9
7.9
Surv.
%
100
92.9
66.4
59.6
lipid,
%
13.2
10
6
6
02b
98
63
81
78
warm - Se control
Sea
1
1.2
1.1
1.2
Surv.
%
100
95.7
95.7
95.7
lipid,
%
13.2
13.3
13.4
13.6
02b
98
98
100
100
ption in Juvenile Bluegill
warm + Se
Sea
1
5.8
6
6
Surv.
%
100
100
96.7
92.6
lipid,
%
13.2
13.3
13.4
13.5
02b
98
103
120
120
a whole body Se tissue concentration, (ig/g dw
b oxygen consumption, mg/kg/hr
* Cumulative Survival: In this experiment, 240 juvenile bluegill were placed in three 400-L fiberglass tanks, 80 in each, and exposed to each
control and treatment for a period of 180 days. Ten fish were removed at random from each treatment replicate on days 0, 60, 120, and 180 for
selenium, histological, hematological, and metabolic measurements.
Replicate and Average Whole-body concentrations (ng/g dry weight) of selenium in juvenile bluegill*
replicate
c+Se
w+Se
c-Se
w-Se
day 0
1
0.87
1.17
0.89
0.99
2
1.21
0.96
3
0.95
0.90
mean
1.01
1.01
0.89
0.99
day 60
1
6.30
5.61
0.97
1.12
2
5.49
6.19
3
5.76
5.43
mean
5.85
5.74
0.97
1.12
day 120
1
8.36
6.37
1.01
0.99
2
7.31
5.92
3
7.85
5.50
mean
7.84
5.93
1.01
0.99
day 180
1
7.53
5.48
1.10
0.96
2
8.01
5.72
3
8.19
6.02
mean
7.91
5.74
1.10
0.96
Each value is for a composite sample made from 5 fish.
1-50 Draft November 12, 2004
-------
The Kaplan-Meier estimator was used to calculate survival at time t
where r(Y,) is the number offish alive just before time tt, i.e. the number at risk, and dt is the number of deaths in the interval/, = [t,, ti+l]. The 95%
confidence interval for such estimate (Venables and Ripley 2002) was computed as
exp<- H(t) exp
±k
where
H(t) =
and j < i
The following table lists the estimates of survival in the cold + Se treatment at 60, 120 and 180 days. The term n.event is the number of deaths at a
given interval; n.risk is the number of organisms alive at the beginning of the interval; survival is computed by the Kaplan-Meier estimator.
Time
60
120
180
n.risk
210
165
88
n. event
15
47
9
survival
0.929
0.664
0.596
std.err
0.0178
0.0350
0.0381
lower 95% CI
0.884
0.590
0.517
upper 95% CI
0.956
0.728
0.666
1-51 Draft November 12, 2004
-------
Hematological Measurements in Juvenile Bluegill Sunfish (*indicates significantly different from control)
Warm Exposure
blood parameter
total erythrocyte, lOVml
% mature
nuclear shadows, 104/ml
total leucocytes, 104/ml
% lymphocytes
% neutrophils
hematocrit, %
MCHC (mean corpuscular hemoglobin cone.)
Cold Exposure
blood parameter
total erythrocyte, lOVml
% mature
nuclear shadows, 104/ml
total leucocytes, 104/ml
% lymphocytes
% neutrophils
hematocrit, %
MCHC (mean corpuscular hemoglobin cone.)
MCV (mean corpuscular volume)
dayO
warm-Se
2.95
85
0.95
17.22
23
15
37
23
warm+Se
2.92
86
0.86
17.41
25
13
36
25
day 0
cold-Se
2.91
84
0.86
16.48
17
13
39
26
182
cold+Se
2.93
82
0.84
16.88
16
12
37
25
171
day 60
warm-Se
2.96
86
0.97
16.90
20
14
37
25
warm+Se
2.93
93*
2.05*
17.55
23
15
29*
19*
day 60
cold-Se
2.97
87
0.83
16.79
16
15
40
25
188
cold+Se
2.90
95*
2.30*
16.91
17
11
30*
18*
146*
day 120
warm-Se
2.99
86
0.83
16.73
19
17
36
25
warm+Se
2.95
94*
2.38*
17.62
26
19
29*
18*
day 120
cold-Se
3.01
85
0.89
16.80
19
15
41
22
180
cold+Se
2.95
96*
2.49*
16.74
15
12
28*
17*
135*
day 180
warm-Se
2.96
85
0.91
17.05
21
17
38
25
warm+Se
2.89
94*
2.30*
17.36
22
16
28*
17*
day 180
cold-Se
3.00
85
0.90
16.96
19
12
39
23
185
cold+Se
2.99
97*
2.36
16.63
18
14
27*
17*
130*
1-52 Draft November 12, 2004
-------
Hermanutz et al. 1996. Exposure of bluegill (Lepomis macrochirus) to selenium in outdoor
experimental streams. U.S. EPA Report. Mid-Continent Ecology Division. Duluth, MN.
Test Organism:
Exposure Route:
Study Design:
Bluegill (Lepomis macrochirus; 3 to 4-year old adults)
Dietary and waterborne followed by dietary only
Dietary and waterborne
Selenite was added to artificial streams which entered the food web; thus, fish
were also exposed to selenium in the diet.
Dietary only
Recovering streams exposed bluegill to selenium in prey organisms. Selenite
addition to water was ceased (selenium in water was below detection level).
Eight Monticello artificial streams were used for three separate studies between
1987 and 1990.
Stream
Dates
BGa put in station 0-2
BG transferred to sta. 6
End of study
1
2
3
4
5
6
7
8
Study I
9-1-87
5-16-88
8-22-88
Unused
Unused
10 Mg/L
30 Mg/L
Control
30 Mg/L
Control
10 Mg/L
Study II
10-88
5-89
8-89
Control
2.5 ng/L
10 Mg/L
Recovering
Control
Recovering
2.5 ng/L
10 Mg/L
Study III
11-89
5-90
7-90
Control
Recovering
Recovering
Recovering
Control
Recovering
Recovering
Recovering
BG = Bluegill.
A schematic diagram of an artificial stream is provided below. For each study, a
random sample of 22-50 adult bluegill were transferred from stations 0-2
(provided temperatures above 4°C during winter) to station 6 (most suitable for
nests) during mid-May for spawning. Spawning activity was monitored in the
streams. Embryo and larval observations were made in situ and in the laboratory
from fertilized eggs taken from the streams and incubated in the lab.
1-53
Draft November 12, 2004
-------
Schematic Design of One of the Artificial Streams in the Monticello Study
Station Number
inlet
" Adults from fall to
mid-May
Adult barrier-
Adult banier-
Adult bamer •
Adults frommid-
„ May to end o f study
Effects Data :
Adult survival in Studies n and III was very low and will not be considered in the
effects analysis. The percent hatch, percent larval survival, percent edema,
percent lordosis and percent hemorrhaging in the 2.5 and 10 (ig/L streams for
Study II are provided in the table below. The values presented in this table aie
corrected values for Study n as reported by Tao et al. (1999). The data from
Study II (both egg cup and field nest) were not amenable for regression analysis.
As reported by Tao et al. (1999), ANOVA was utilized to evaluate effects of
elevated concentrations of selenium on percent hatch, percent survival, maximum
percent edema, lordosis, and hemorrhage, and minimum percent healthy (egg cup
data). Treatment effects were only significant for maximum percent edema and
minimum percent healthy (see their Table 4-19), and in no instance were
1-54
Draft November 12, 2004
-------
differences between the 2.5 (ig Se/L and control treatments significant (Dunnett's
Means test, all probabilities > 0.1, see their Table 4-20). These results clearly
suggest that the 2.5 (ig Se/L treatment had no adverse impact on bluegill larvae.
They are further supported by analysis of the field nest data (see table below). In
this experiment, treatment had a significant effect on maximum percent edema
(raw data and ranks) and maximum percent hemorrhage (ranks only).
Probabilities of differences between the 2.5 (ig Se/L and control treatments were
>0.2 for all response variables except maximum percent hemorrhage, which had
an estimated probability of 0.05 (raw data, />=0.022 for ranks; Dunnett's means
test). Such values, though, were well above the adjusted experiment-wise error
rate for multiple comparison (a'=0.0085, a'=l-(l-a)1/t; a=0.05, k=6 comparisons;
Sokal and Rohlf 1981), which takes into account the fact that selenium effects
were tested on six different response variables. Therefore, the chronic value for
this study, 12.12 (ig Se/g dry weight, was calculated as the geometric mean of
tissue concentrations of selenium in the 2.5 (NOAEC) and 10 (ig Se/L (LOAEC)
treatments (5.55 and 26.46 (ig Se/g dw whole bodytissue, respectively).
Chronic Value: 12.12 (ig Se/g dw whole-body tissue, calculated as the GM of the NOAEC, 5.55
(ig Se/g dw, and LOAEC, 26.46 (ig Se/g dw, based on percent larval survival and
percent larvae exhibiting edema in the egg cup exposures. Note: the NOAEC
value of > 17.35 (ig Se/gdw was selected as the chronic value for Study III based
on percent larval survival in egg cup exposures and percent larvae exhibiting
edema in nest observations.
1-55 Draft November 12, 2004
-------
Effects on Progeny - Study IIab
Egg cup observations
treatment
control
control
2.5 Mg/L
2.5 Mg/L
10 Mg/L
10 ng/L
rec 30 (ig/L
rec 30 pig/L
stream
1
5
2
7
3
8
4
6
number of
trials
6
5
0
4
3
2
0
6
% hatch
93.0
96.4
NA
81.4
83.3
91.1
NA
92.9
% survival
to 3rd day
75.2
71.5
NA
71.6
57.7
57.1
NA
73.0
% edema
0
0
NA
0
100
100
NA
17.4
% lordosis
0
0
NA
0
11.1
18.2
NA
0
% hemorr
0
0
NA
3.6
49.3
41.1
NA
11.5
whole-body Se
(Hg/g dw)
2.05
1.85
6.8
5.55
20.75
33.75
NA
30.6
Nest Observations
treatment
control
control
2.5 ng/L
2.5 Mg/L
10 Mg/L
10 Mg/L
rec 30 (ig/L
rec 30 ng/L
stream
1
5
2
7
3
8
4
6
# active
nests
6
9
1
5
2
3
0
8
# embryos
collected
2458
1329
0
1462
672
931
NA
646
% dead
embryos
0.94
0
0
0
0.32
NA
0
# larvae
collected
3252
3435
2497
4717
5376
750
NA
6782
% dead
larvae
0.03
1.05
0.20
0.08
0.50
0.40
NA
7.8
#samples
w larvae
7
13
3
8
9
4
NA
16
% edema
0
0
4.1
0
81.4
50
NA
27.3
% lordosis
0
0
25
0
5.0
14.7
NA
0
% hemorr
0
0
77.6
52
55.5
26.7
NA
17.1
whole-body Se
((ig/g dw)
2.05
1.85
6.8
5.55
20.75
33.75
NA
30.6
a Values in table were taken from Tao et al. (1999).
b The chronic value for the study was calculated as the GM of whole-body selenium concentrations in the 2.5 (NOAEC 5.55 (ig Se/g dw;
stream 7 only) and 10 (ig Se/L (LOAEC of 26.46 (ig Se/g dw; GM of streams 3 and 8, respectively) treatments in the egg cup exposures.
1-56 Draft November 12, 2004
-------
Effects on Progeny - Study IIP
Egg cup observations
treatment
control
control
rec 2.5 (ig/L
rec 2.5 (ig/L
rec 10 (ig/L
rec 10 (ig/L
rec 30 (ig/L
rec 30 (ig/L
Stream
1
5
2
7
3
8
4
6
number of
trials
2
3
3
6
3
5
% hatch
92
76.7
87.3
87.2
75.3
92
% survival to
3rd day
58.6
69.2
66
76.5
74.5
78
% edema
0
0
0
0
0
% lordosis
0
0.9
0
0
0
% hemorr
0
0.8
0
0
0
whole- body
Se ((ig/g dw)
1.6
3.35
5.25
5.35
14.5
11.7
17.35
Nest observations
treatment
control
control
rec 2.5 (ig/L
rec 2.5 (ig/L
rec 10 (ig/L
rec 10 (ig/L
rec 30 (ig/L
rec 30 (ig/L
stream
1
5
2
7
3
8
4
6
# active nests
2
2
5
5
2
4
9
# samples with
larvae
5
3
5
2
4
4
13
% edema
0
0
0
0
0
0
0
% lordosis
0
0
0
0
0
0
0
% hemorr
0
0
0
0
0
0
0
whole-body Se
((ig/g dw)
1.6
3.35
5.25
5.35
14.5
11.7
17.35
The chronic value for the study was selected as the NOAEC of >17.35 pg Se/g dwfrom the recovering 30 pg Se/L treatment.
1-57 Draft November 12, 2004
-------
Coughlan, D.J. and J.S. Velte. 1989. Dietary toxicity of selenium-contaminated red shiners to striped
bass. Trans. Am. Fish Soc. 118:400-408.
Test Organism:
Exposure Route:
Test Treatments:
Test Duration:
Study Design:
Effects Data:
Striped bass (Morone saxitilis; adults from Lake Norman, NC, approximately 250
g each)
dietary only
Treated fish were fed selenium contaminated red shiners (1 g) from BelewsLake,
NC (9.6 (ig Se/g ww or 38.6 (ig Se/gdw based on amean reported moisture
content of 75.1 percent). Control fish weie fed golden shiners from a local bait
dealer (0.3 (ig Se/g ww or 1.3 (ig Se/g dw based on amean reported moisture
content of 76.3 percent).
Test treatments were as described above. Two tanks contained treated fish (n =
20 fish total), and one tank offish served as the control (n = 10 fish). Each tank
received a continuous flow of soft well water (hardness and alkalinity approx. 30
mg/L as CaCO3) throughout the exposure.
80 days
During the experiment, all striped bass (n = 10 per tank) were fed to satiation
three times per day. Pre-weighed rations of live red shiners (treated fish) and
golden shiners (controls) were added to the tanks and allowed 5 hours to feed.
Uneaten prey was removed and weighed. Composite whole-body samples of each
prey fish were collected at regular intervals throughout the study for whole-body
tissue selenium analysis. The final selenium concentration in epaxial white
muscle was determined for surviving striped bass at the end of the test. Moribund
striped bass were sacrificed so as to obtain muscle tissue samples for selenium
analysis. Samples of liver and trunk kidney of these and the surviving striped
bass were dissected for observations of histopathology.
Striped bass fed selenium-laden red shiners exhibited changes in behavior
(lethargy, reduced appetite), negligible weight gain, elevated selenium
concentrations in muscle, histological damage, and death. Control fish ate and
grew well, and behaved normally. Average selenium ingestion was between 60
and 140 (ig Se/fish per day until day 30. Appetite of the treated fish appeared to
be significantly reduced beyond this point compared to the appetite of the control
group. By day 78, all striped bass fed the Se-laden red shiners either had died or
were moribund and sacrificed for analysis. The final selenium concentration in
muscle of treated striped bass averaged from 3.5 (tank 1) and 4.0 (tank 2) (ig/g
ww, or 17.5 and 20.0 (ig/g dw, respectively, assuming SOpercent moisture
content in muscle tissue. The final selenium concentration in muscle of control
striped bass fed uncontaminated golden shiners averaged 1.1 (ig/g ww, or 5.50
(ig/g dw (assuming 80 percent moisture content in muscle tissue).
1-58
Draft November 12, 2004
-------
Chronic Value: The chronic value for percent survival of striped bass relative to final selenium in
muscle tissue after being fed Se-laden red shiners is <17.50 (ig/g dw, or 14.75
(ig/g dw whole body tissue converted using equation I.
An EC20 value could not be calculated for this data set because the data did not
meet the assumptions required for analysis.
1-59 Draft November 12, 2004
-------
Lemly, A.D. 1993b. Teratogenic effects of selenium in natural populations of freshwater fish.
Ecotoxicol. Environ. Safety. 26: 181-204.
Test Organism:
Exposure Route:
Study Design:
Effects Data :
Chronic Value:
All possible fish species collected from Belews Lake and a reference site.
dietary and waterborne - field exposed
Surveys of external abnormalities in fish collected from Belews Lake and two
reference lakes were done in 1975, 1978, 1982, and 1992. Five classifications of
abnormalities were reported: (1) spinal deformities (lordosis, scoliosis, kyphosis);
(2) accumulation of body fluid (edema, expothalmus or popeye); (3) missing or
abnormal fins; (4) abnormally shaped head or mouth; and (5) cloudy eye lens or
cornea (cataracts). Whole-body selenium was measured in each fish. The
relationship between whole-body selenium and malformations was examined.
The relationship between whole-body selenium and the frequency of
malformations in all the fish species collected at Belews (n=22) did not follow a
clear trend. When evaluating only fish from the family Centerchidae using a
polynomial regression (cubic model) an R2 value of 0.881 was obtained. Lemly
reported that the inflection point where a rapid rise in deformities occurred was
between 40 and 50 (ig Se/g dw in whole-body tissue. The EC20 value determined
by regression analysis of percent normal fish versus whole-body tissue selenium
concentration for the family Centrarchidae (most sensitive family or group of
families) was 44.57 (ig Se/gdw. Centrarchidae was the most sensitive family or
group of families of those collected during the survey.
The EC20 value determined by regression analysis of percent normal fish versus
whole-body tissue selenium concentration for the family Centrarchidae was 44.57
(ig Se/g dw.
1-60
Draft November 12, 2004
-------
Centrarchidae (Lemly 1993)
1.0 -
g °-8
tf
o
Q.
P 0,6
0.4 -
0.2
0.0
1.0
2 3 4567 810.0
2 3 4567
Tissue Se[^ig/g dw]
1-61
Draft November 12, 2004
-------
APPENDIX J
SELENIUM (ug/g dw WHOLE-BODY) IN FISH SAMPLES COLLECTED FROM 112
SITES AS PART OF U.S. FISH AND WILDLIFE3 NATIONAL BIOMONITORING
PROGRAM, 1978-1981 (LOWE ET AL. 1985).
AND
SELENIUM (ug/g dw WHOLE-BODY) IN 322 AQUATIC LIFE TISSUE SAMPLES
COLLECTED FROM 264 SITES AS PART OF USGS NATIONAL WATER QUALITY
ASSESSMENT (NAWQA) PROGRAM
(http://water.usgs.gov/nawqa/ as of May 11, 2004).
J-1 Draft November 12, 2004
-------
FCV Relative to Natural Background Levels of Selenium in Fish
As an essential element, selenium naturally occurs in all living things. Since selenium is found in all fish,
two questions arise. 1) How close is the FCV of 7.91 (ig/g dw to natural background levels in fish, and 2)
how frequently do natural selenium tissue concentrations exceed the FCV. The latter situation would pose
problems in the implementation of the FCV as an ambient water quality criterion.
As part of the National Contaminant Biomonitoring Program, the U.S. Fish and Wildlife Service collected
fish from 112 sites distributed evenly across the U.S. during 1979 through 1981, and measured several
contaminants including selenium (Lowe et al. 1985). Selenium, measured in 591 fish samples representing
60 different species, ranged from 0.3 to 10.5 (ig/g dw and had an overall average and standard deviation of
1.9± 1.4(ig/gdw.
A separate data set of selenium levels in 231 macroinvertebrate samples, 90 fish samples, and one plant
sample collected from 25 different states across the United States was generated by USGS's National
Water Quality Assessment (NAWQA) program. NAWQA is intended to measure water quality in a
sampling of smaller watersheds having known land use. Among these sites, whole body tissue
concentrations ranged from 0.3 to 22.37 (ig/g dw and had an overall average and standard deviation of 3.22
± 2.29 (ig/g dw. The distribution of both these data sets indicates that the FCV would not be exceeded by
over 97 percent of aquatic tissue samples collected across the United States (Figure J-l). The FCV thus
appears to be sufficiently greater than natural selenium levels that unavoidable exceedances of the criterion
are unlikely.
J-2 Draft November 12, 2004
-------
Distribution of selenium concentrations in whole body
<).986
1.0 -*
.2 0.8
o
Q.
O 0.6
Q.
0)
£ 0.4
O
0.2
0.0
0
-National Contaminant Biomonit. Pgm (fish
samples) n = 591
- USGS NAWQA Sites (fish and invertebrate
samples) n = 322, 64 nondetects (19.9%)
Chronic criterion
7.9jug/gdw
5 10 15 20
Se in whole body [M9/9 dw]
25
Figure J-l. Cumulative distribution of selenium concentrations in aquatic organisms (whole-body, (ig/g
dw) collected by the National Contaminant Biomonitoring Program (NCBP) and the U.S.
Geological Service National Water-Quality Assessment (NAWQA) Program. NCBP and
NAWQA data from Lowe et al. (1985) and query results from NAWQA's database on
contaminant concentrations in animal tissues (http://water.usgs.gov/nawqa/), respectively.
J-3
Draft November 12, 2004
-------
Table J-l. Selenium (ng/g dw whole-body) in fish samples collected from 112 sites as part of U.S. Fish and
Wildlife's National Biomonitoring Program, 1978-1981. From Lowe et al. 1985
Year Species
Mean total length, cm
Mean total weight, Kg
Se, ug/g dry wt.
78
78
78
80
80
80
78
78
78
80
80
80
78
78
78
80
80
79
79
79
81
81
81
79
79
79
81
81
81
79
79
79
81
81
81
Smallmouth bass
White sucker
White sucker
Smallmouth bass
White sucker
White sucker
White catfish
White catfish
Yellow perch
White catfish
White catfish
Yellow perch
Goldfish
Goldfish
Largemouth bass
Goldfish
Largemouth bass
White perch
White sucker
White sucker
Largemouth bass
White sucker
White sucker
Common carp
Common carp
White perch
Common carp
Common carp
White perch
Common carp
Common carp
Smallmouth bass
Largemouth bass
Redhorse
Redhorse
Station 1, Penobscot River at Old Town, MA
Station
12.9
13.7
14.4
12.8
15.2
15.3
2, Connecticut River at Windsor Locks, Conn.
16.6
16.5
8
14.5
13.3
9.5
Station 3, Hudson River at Poughkeepsie, NY
11
11.4
11.1
10.9
14.8
Station 4, Delaware River at Trenton, NY- Yardley, Pa
7.3
Station
Station 6
12.8
14.3
9.5
15
14.4
5, Susquehanna River at Conowingo Dam, Md.
12.9
16.9
7.6
14.4
14.1
7.9
1.2
1.1
1.3
1.1
1.3
1.4
2.3
2.3
0.3
0.9
0.9
0.4
1
1.1
0.8
1
2.2
0.2
0.8
1.2
0.4
1.3
1.1
2
2.3
0.3
1.6
1.7
0.3
0.8562
1.2227
0.9292
0.6513
0.8261
0.7634
0.4651
0.6818
0.9934
0.6007
0.9738
0.9811
0.9353
0.6545
1.0676
1.2333
1.0701
4.6429
1.1438
0.8389
2.4206
1.1864
1.4423
2.0690
2.2381
5.5401
2.5431
1.5358
3.4951
, Potomac River at Little Falls Md.- McLean Va
18.7
17
10
11.5
17.2
17.5
3.1
2.5
0.5
8
2
2.1
1.5248
1.1628
2.6587
1.8474
1.2963
1.3208
Station 7, Roanoke river at Roanoke Rapids, N.C.
J-4
Draft November 12, 2004
-------
Year Species
Mean total length, cm
Mean total weight, Kg
Se, ug/g dry wt.
78
80
80
80
78
78
80
80
80
78
78
80
80
80
78
78
80
80
80
78
78
78
80
80
80
79
79
79
81
81
81
79
79
81
81
81
White catfish
Striped bass
White catfish
White catfish
Spotted sucker
Spotted sucker
Flathead catfish
Quillback
Quillback
Channel catfish
Channel catfish
Channel catfish
Channel catfish
Striped bass
Channel catfish
White catfish
White catfish
White catfish
Bowfin
Largemouth bass
White catfish
White catfish
Largemouth bass
White catfish
White catfish
Largemouth bass
Spotted sucker
Spotted sucker
Largemouth bass
Spotted sucker
Spotted sucker
Smallmouth buffalo
Smallmouth buffalo
Black crappie
Blue catfish
Blue catfish
12.7
14.5
11.7
10.1
0.7
1.4
0.6
0.4
Station 8, Cape Fear River at Elizabethtown, NC
16.3 2
16 2
19 2
15 1.7
14.9 1.1
Station 9, Cooper River at Lake Moultrie, Monck;s Coner, S.C
16.3 1.3
14.6
14.5
13.6
20.6
1
1
0.6
3.3
Station 10, Savannah River at Savannah, Ga
11 0.4
12.7 1
11.3 0.7
7.9 0.2
21 3.6
Station 12, St. Lucie Canal at Indiantowm, Fla
Satation 13, Appalachicola River at J. Woodruff Dam, Fla.
Station 14, Tombigbee Tiver atMcIntosh, Ala.
1.2134
1.3665
1.0473
1.0164
2.5177
2.5263
1.0656
1.6719
1.6558
1.6078
1.4563
1.4497
1.4917
1.4894
3.2444
2.0248
1.4592
1.2319
2.2568
Station 15, Mississippi Tiver at Luling, La.
J-5
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
79
79
79
81
81
81
80
80
80
81
81
81
80
80
80
81
81
81
78
79
79
81
81
81
80
80
80
79
79
79
81
81
81
79
79
79
81
Common carp
Common carp
Largemouth bass
Channel catfish
Channel catfish
Largemouth bass
Gizzard shad
Gizzard shad
Largemouth bass
Common carp
Gizzard shad
Gizzard shad
Pumpkinseed
Redhorse
Redhorse
Pumpkinseed
Redhorse
Redhorse
Rock bass
Yellow perch
Yellow perch
Rock bass
Yellow perch
Yellow perch
Redhorse
Redhorse
Yellow perch
Common carp
Common carp
Yellow perch
Common carp
Common carp
Yellow perch
Bloater
Bloater
Lake trout
Bloater
Station 16, Rio Grande at Mission, Tex
Station 17, Genessee River at Scottsville, NY
Station 18,, Lake Ontario at Prot Ontario, NY
Station 19, Lake Erie at Erie, Pa
Station 20, Lake Huron (Saginaw Bay) at Bay port, Mich.
Station 21, Lake Michigan at Sheboygan, Wis.
1.6667
1.7162
1.7200
0.6599
0.7561
1.8147
2.4638
2.4719
2.2800
2.1858
2.6190
2.8125
1.7625
1.7241
2.4576
0.8060
0.6897
1.1730
0.7104
J-6
Draft November 12, 2004
-------
Year Species Mean total length, cm Mean total weight, Kg Se, ug/g dry wt.
81 Bloater 0.9687
81 Laketrout 1.2828
Station 22, Lake Superior at Bayfield, Wis.
79 Laketrout 0.8911
79 Lake whitefish 1.3278
79 Lake whitefish 1.5058
81 Bloater 1.1304
81 Bloater 1.3419
81 Laketrout 1.4741
Station 23, Kanawha River at Wmfield, W. VA
78 Channel catfish
78 Channel catfish
78 Sauger
80 Channel catfish
80 Channel catfish
80 Sauger
Station 24, Ohio River at marietta, Ohio- Wilhamstown, W VA
78 Channel catfish 1.1871
78 Sauger 1.4716
80 Common carp 2.2819
80 Common carp 1.7687
80 Sauger 2.2511
Station 25, Cumberland River at Clarksville, Term.
78 Common carp
78 common carp
78 White catfish
80 Common carp
80 Common carp
80 Largemouth bass
Station 26, Illinois River at Beardstown, 111.
78 Black crappie
78 Common carp
78 Common carp
80 Black crappie
80 Common carp
80 Common carp
Station 27, Mississippi River at Gutenburg, Iowa- Glen Haven, Wis.
78 Common carp 1.7628
78 Common carp 1.3907
78 Largemouth bass 2.2742
80 Common carp 1.3231
80 Common carp 0.9064
80 Largemouth bass 1.1885
J-7 Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Station 28, Arkansas River at Pine Bluff, Ark.
Se, ug/g dry wt.
79
79
79
81
81
81
79
79
79
81
81
81
79
79
79
81
81
79
79
79
81
81
81
79
79
81
81
81
79
79
79
81
81
78
78
78
80
Bluegill
Common carp
Common carp
Common carp
Common carp
Largemouth bass
Common carp
Common carp
White bass
Common carp
Common carp
White crappie
Freshwater drum
Freshwater drum
Largemouth bass
Common carp
Common carp
Common carp
Common carp
Goldeye
Common carp
Common carp
Goldeye
Northern pike
Redhorse
Walleye
White sucker
White sucker
Brown trout
White sucker
White sucker
Brown trout
White sucker
Common carp
Common carp
Sauger
Mooneye
Station 29, Arkansas River at Keystone Reservoir, Okla.
Station 30, White River at De Vails Bluff, Ark.
Station 31, Missouri River at Nebraska City, Nebr.- Hamburg, Iowa
Station 32, Missouri River at Garrison Dam, N Dak.
Station 33, Missouri River at Great Falls Mont.
Station 34, Red River of the Norh at Noyes, Minn. _ Pembina, N. Dak.
1.3974
1.6509
2.2167
2.2394
1.3410
1.0738
0.8874
0.9091
0.8696
2.2857
1.7472
1.8774
2.8163
1.2712
3.0189
3.2051
3.1803
1.4884
0.9600
1.6041
2.4883
3.9252
2.3432
1.3333
1.3158
2.1591
1.9617
2.3166
2.0629
0.4682
3.3754
J-8
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
80
80
78
78
78
80
80
80
78
78
78
80
80
80
80
80
80
81
78
78
78
80
80
80
79
79
79
81
81
79
79
79
81
81
78
78
Sauger
Sauger
Common carp
Common carp
Smallmouth bass
Common carp
Common carp
Smallmouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Green sunfish
Tahoe sucker
Tahoe sucker
Green sunfish
Common carp
Common carp
White bass
Common carp
Common carp
White bass
Brown bullhead
Largemouth bass
largescale sucker
largescale sucker
Largemouth bass
Black bullhead
Black bullhead
Green sunfish
Sacramento blackfish
Sacramento blackfish
Largescale sucker
Largescale sucker
Station 35, Green River at Vernal, Utah
Station 36, Colorado River at Imperial Reservoir, Ariz.- Calif.
Station 37, Truckee River at Fernley, Nev.
Station 38, Utah lake at Provo, Utah
Station 39, Sacramento River at Sacramento, Calif.
Station 40, San Joaquin River at Los Banos, Calif.
Station 41, Snake River at Hagerman, Idaho
0.9328
0.8117
3.7410
3.9286
3.6076
3.2537
2.7811
3.1500
6.5552
8.0364
10.5204
7.5210
6.4783
8.6531
1.0794
0.9211
1.1401
0.8835
0.7035
1.2644
1.0811
1.2454
1.4286
1.2431
1.4126
J-9
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
78 Rainbow trout
80 Largescale sucker
80 Largescale sucker
80 Rainbow trout
2.3630
1.3913
1.5447
1.9495
Station 42, Snake River at Lewiston, Idaho- Clarkston, Wash.
78
78
78
80
80
80
Largescale sucker
Largescale sucker
Smallmouth bass
Largescale sucker
Largescale sucker
White crappie
Bridgelip sucker
Bridgelip sucker
Northern squawfish
Bridgelip sucker
Bridgelip sucker
Northern squawfish
Station 43, Salmon River at Riggins, Idaho
1.5719
0.8494
1.1930
0.9016
0.8475
2.9897
Station 44, Yakima River at Granger, Wash.
78 Common carp
78 Common carp
80 Black crappie
80 Largescale sucker
80 Largescale sucker
2.3026
1.4047
1.6716
1.7742
1.6508
Northern squawfish
Chiselmouth
Chiselmouth
Largescale sucker
Largescale sucker
Northern squawfish
Station 45, Willamette River at Oregon City, Ore;
0.5078
0.6615
0.4082
0.5479
0.6907
1.4286
78
78
78
80
80
80
Largescale sucker
Largescale sucker
Northern squawfish
Largescale sucker
Largescale sucker
Northern squawfish
Station 46, Columbia River at Cascade Locks, Wash. -Oreg.
1.2684
1.3712
1.7818
0.9236
0.6765
0.7025
79 Klamath largescale sucker
79 Klamath largescale sucker
79 Yellow perch
81 Klamath largescale sucker
Station 47, Klamath River at br k, Calif
J-10
Draft November 12, 2004
-------
Year Species Mean total length, cm Mean total weight, Kg Se, ug/g dry wt.
81 Yellow perch 0.9016
Station 48, Rogue River at G )Id, y Da Oreg.
79 Black crappie
79 Redside shine
81 Black crappie
81 Brown bullhead
81 Brown bullhead
Station 49, (,hena River at rks, aska
79 Burbot 2.3005
79 Longnose sucker 1.2903
81 Longnose sucker 1.7757
81 Longnose sucker 1.8519
81 Northern pike 1.8026
Station 50, Kenai River at SDidatna, laska
78 Rainbow trout 2.0391
78 Round whitefish 2.9538
78 Dolly Varden 1.6992
80 Rainbow trout 1.8910
80 Round whitefish 1.8954
80 Dolly Varden 1.6910
Station 51, Kennebec Rive at iiic y, Maine
78 White sucker 1.1060
78 White sucker 0.9692
78 Yellow perch 1.2549
80 White sucker 1.0046
80 White sucker 0.9459
80 Yellow perch 0.7011
Station 52 Lake Champlain Burlic gton, Vt.
78 Northern pike 0.7451
78 White sucker 0.8400
78 White sucker 0.8676
80 Northern pike 1.1163
Station 53, Menimack River t Low@ll, Mass.
78 Largemouthbass 0.8070
78 White sucker 1.0357
78 White sucker 1.0676
80 Smallmouth bass 0.7343
80 White sucker 0.8230
80 White sucker 1.2389
Station 54, Rantan River at Highland Park, N. J.
78 Largemouthbass 1.8060
78 White sucker 1.9454
J-11 Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
78
80
80
80
79
79
79
81
81
81
80
80
80
78
78
80
80
80
79
79
79
81
81
81
79
79
79
79
79
79
78
78
78
80
80
White sucker
White sucker
White sucker
Redfin pickerel
Redhorse
Redhorse
Smallnouth bass
Redhorse
Redhorse
Smallnouth bass
Gizzard shad
Gizzard shad
Largemouth bass
Black crappie
Carp sucker
Largemouth bass
Spotted sucker
Spotted sucker
Smallmouth buffalo
Smallmouth buffalo
Bowfin
Largemouth bass
Blue catfish
Blue catfish
Longnose gar
Smallmouth buffalo
Smallmouth buffalo
Channel catfish
Freshwater drum
Freshwater drum
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Station 55, James River at Richmond, Va.
Station 56, Pee Dee River at Johnsonville, S.C.
Station 57, Altamaha River at Doctortown, Ga.
Station 59, Alabama Rive'r at Chrysler, Ala.
Station 60, Brazos River a@ Richmond, Tex.
Station 61, Colorado River at Wharton, Tex.
Station 63, Rio Grande at Elephant Butte, N. Mex.
1.8301
1.5126
2.3348
1.6450
1.2877
1.4194
1.8657
1.9243
1.0658
1.0359
1.2857
1.2342
1.7094
2.0408
1.5574
0.9662
1.7844
1.4943
2.1514
1.9028
1.9310
1.7597
1.5830
J-12
Draft November 12, 2004
-------
Year Species
80 Largemouth bass
78
78
80
80
80
78
78
80
80
80
79
79
79
81
78
78
78
79
79
79
80
80
80
78
78
78
80
80
80
78
78
78
80
80
80
White sucker
White sucker
Brown trout
White sucker
White sucker
Gizzard shad
White bass
Gizzard shad
Gizzard shad
White bass
Smallmouth bass
White sucker
White sucker
Northern pike
Redhorse
Redhorse
Smallmouth bass
Largemouth bass
Redhorse
Redhorse
Redhorse
Redhorse
Smallmouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Sauger
Common carp
Common carp
Sauger
Mean total length, cm Mean total weight, Kg
Station 64, Rio Grande at Alamosa, Colo.
Station 65, Pecos River at Red Bltrff Lake, Tex.
Station 66, St. Lawrence River at Massena, NY.
Station 67, Allegheny River at Natrona, Pa.
Station 68, Wabash River at New Harmony, -Crossville, III
Station 69, Ohio River at Cincinnati, Ohio
Se, ug/g dry wt.
1.5709
0.7442
0.9231
1.2775
0.6911
0.8036
4.2715
9.5016
3.8559
5.0673
6.0681
1.1765
1.0280
1.4414
1.3592
2.0155
1.4232
2.2794
1.3693
1.9005
1.5789
2.7511
2.8139
2.2656
2.0505
2.2302
2.3413
1.3043
1.4873
1.5175
2.5890
4.0333
1.5031
2.1071
2.6070
1.5113
J-13
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Station 70, Ohio River at Metropolis Ill.-Paducah, Ky.
78
78
78
80
80
80
78
79
79
80
80
80
80
80
80
78
78
78
80
80
80
78
78
80
80
80
78
78
78
80
80
80
79
79
79
81
81
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
White bass
Common carp
Carp sucker
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Sauger
Common carp
Common carp
Channel catfish
White sucker
Yellow perch
rock bass
Yellow bullhead
Yellow bullhead
Common carp
Common carp
White crappie
Common carp
Common carp
White bass
Bluegill
Smallmouth buffalo
Smallmouth buffalo
Smallmouth buffalo
Smallmouth buffalo
Station 71, Tennessee iver at Savannah, Term.
Station 72, Wisconsin River at Woodman, Wis.
Station 73, Des Moines River at Keosauqua, Iowa
Station 74, Mississippi River at Little Falls, Minn.
Station 75, Mississippi River at Cape Girardeau, Mo.-Ill
Station 76, Mississippi River
Se, ug/g dry wt.
2 2222
1.4067
1.3514
2.2118
2.0599
1.7770
1.4610
2.3790
1.3333
2.1973
1.8103
1.9178
1.4107
1.1688
1.1538
3.5986
4.0956
2.4706
3.8462
2.3221
1.7883
1.4340
1.5825
1.6207
2.0155
1.9149
2.3511
2.1019
1.2360
1.4449
1.8077
2.8839
1.8000
0.6818
0.6140
1.0979
0.9884
J-14
Draft November 12, 2004
-------
Year
81
79
79
79
81
81
81
79
79
79
81
81
81
79
79
81
81
81
79
79
79
81
81
81
79
79
79
81
81
81
79
79
79
79
79
79
Species
White crappie
Common carp
Common carp
White bass
Bluegill
Common carp
Common carp
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Smallmouth buffalo
Smallmouth buffalo
White crappie
Smallmouth buffalo
Smallmouth buffalo
White bass
Freshwater drum
Freshwater drum
Spotted gar
Black crappie
River carpsucker
River carpsucker
Common carp
Common carp
Largemouth bass
River carpsucker
River carpsucker
Smallmouth buffalo
Common carp
Goldeye
White sucker
Mean total length, cm Mean total weight, Kg
Station 78, Verdigris River at Oologah Okla.
Station 79, Canadian River at Eufaula, Okl.
Station 80, Yazoo River at Redwood, Miss
Station 81, Red River at Alexandria.
Station 82, Red River at Lake Texoma, Okla.-Tex.
Station 83, Missoun River at Hermann, Mo.
Station 84, Bighorn River at Hardin, Mont.
Se, ug/g dry wt.
0.9343
1.0268
1.4218
1.9907
1.7063
2.1223
2.1456
1.1620
2.7356
1.1875
1.3559
1.4444
0.9121
1.1350
1.4706
5.6522
9.4118
6.9466
J-15
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
81
81
79
79
79
81
81
81
79
79
79
81
81
81
79
79
79
81
81
81
79
79
79
81
81
79
79
79
81
81
81
79
79
81
81
81
Brown trout
Longnose sucker
Common carp
Common carp
Sauger
Redhorse
Redhorse
Sauger
Carp sucker
Carp sucker
Goldeye
Carp sucker
Carp sucker
Goldeye
Common carp
Common carp
Walleye
Common carp
Common carp
Walleye
Black crappie
Common carp
Common carp
White sucker
Orangespotted sunfish
Carp sucker
Carp sucker
Goldeye
Carp sucker
Carp sucker
Goldeye
Common carp
River carpsucker
Common carp
Channel catfish
River carpsucker
Station 85, Yellowstone River at Sidney,Mont.
Station 86, James River at Olivet, S. Dak
vet, S. ak.
Station 87, North Platte River at Lak McConaughy, Nebr.
Station 88, South Platte River at Brule, Nebr.
Station 89, Platte River at Lduisville Nebr.
Station 90, Kansas River at
onner prings, Kans.
5.0896
3.0717
1.4773
1.9277
1.7257
1.8919
2.4832
1.6832
1.7188
1.9184
1.7302
1.0154
1.2805
2.5185
3.7288
4.8918
1.4907
3.0488
2.6601
2.0077
2.7881
4.3902
4.3590
4.6538
8.6786
2.2549
1.6514
3.2335
2.5207
2.8270
4.0972
2.4615
1.0676
1.5858
2.1635
0.9859
Station 91 Colorado River at Lake Havasu, Ariz.-Calif.
J-16
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
78
78
80
80
80
79
79
79
81
81
81
78
78
80
80
80
78
78
78
80
80
80
78
78
78
80
80
80
78
78
78
80
80
80
78
78
78
80
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Channel catfish
Channel catfish
Striped bass
Common carp
Channel catfish
Striped bass
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Common carp
Common carp
Largemouth bass
Largescale sucker
Largescale sucker
Northern squawfish
Largescale sucker
Largescale sucker
Northern squawfish
Yellow perch
Chiselmouth
Chiselmouth
Common carp
Common carp
Yellow perch
Largescale sucker
Largescale sucker
Yellow perch
Largescale sucker
Station 92, Colorado River at Lake Mead Anz.-Nev.
Station 93, Colorado v" tLake 11, Ariz.
Station 94, Gfla River at Sa
"IIDI servoir, Ariz.
Station 96, Snake River at I H @b, 'D.@'oWasri
Station 97, Columbia River Pa,,O, sh.
Station 98, Columbia i,er G @,n 'C.uloee, Wash.
7.6490
5.1449
3.6494
5.6944
2.7666
4.6441
3.0169
0.8182
3.3735
3.2707
3.7109
9.4218
9.8990
4.3922
3.9574
2.3759
1.9231
1.5918
1.7466
1.9588
1.4079
1.1524
1.0000
1.2625
0.8970
0.8765
0.8456
1.7316
3.8667
1.6242
1.2375
4.0244
2.6923
3.5662
0.8300
0.9266
1.1847
0.7692
J-17
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
80 Largescale sucker
80 Walleye
0.7519
0.8108
79 Cuban limia
tation 99, Waikele Stea, Waipah Hawaii
4.0755
79
79
78
78
78
80
80
80
79
79
79
81
81
81
79
79
79
81
81
79
79
79
79
79
79
81
81
81
79
79
79
Cuban limia
Mazambique tilapia
White sucker
White sucker
Yellow perch
White sucker
White sucker
Yellow perch
Bloater
Bloater
Lake trout
Bloater
Bloater
Lake trout
Lake trout
Lake whitefish
Lake whitefish
Lake trout
Lake whitefish
Bloater
Bloater
Lake trout
Bloater
Bloater
Lake trout
Bloater
Bloater
Lake trout
White sucker
White sucker
Yellow perch
Station 100, Manoa Stream at Honol Hawai
Station 101, Androscoggin iver at wiston, Main
Station 1 02, Laice Superior at@Keewe@naw Point, Mich.
Station 1 03, Lake Superior at Whitefish Point, Mich.
104, Lake Michigan at Beavei,lsland,Mich.
Station 105. Lake Michigan at Saugat@ck, Mich
Station 106, Lake Huron at Alpena Mich.
3.5577
1.6502
0.9426
0.7059
0.7042
0.6299
0.5691
0.8961
0.7427
1.1379
1.8051
1.0617
1.4947
0.8537
0.4963
1.3483
0.4948
0.6651
0.8310
0.8696
0.8939
1.1480
J-18
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
81
81
81
79
79
79
81
81
81
79
79
79
81
81
81
79
79
79
81
81
81
78
78
80
80
80
78
78
78
80
80
80
79
78
78
78
Lake trout
White sucker
White sucker
Common carp
Common carp
Walleye
Common carp
Common carp
Walleye
Common carp
Common carp
Walleye
Common carp
Common carp
Walleye
Brown trout
Rock bass
Rock bass
Lake trout
Rock bass
Rock bass
White sucker
White sucker
Walleye
White sucker
White sucker
Common carp
Common carp
Largemouth bass
Black crappic
Common carp
Common carp
Longnose gar
Common carp
Common carp
Channel catfish
Station 107, Lake St. Glair at Mount Clements. Mich.
Station 108, Lake Erie at Port Clinton. Ohio
Station 109, Lake Ontario at Roosevelt Beach, N.Y.
Station III. Mississippi River at Lake City, Minn.-Pepin. Wis.
Station 112, Mississippi River at Dubuque, Iowa
12.9 1.1
14.4 1.5
11.2 1.1
10.2 0.7
17 2.6
17.8 3
Station 113, San Antonio River at McFadden, Tex.
28.5 2.3
Station 114, Bear River at Brigham City, Utah
11.7
10.2
17.9
0.6
2.3
1.2808
2.3293
2.2403
1.2030
1.6418
1.7731
1.8182
2.0861
1.9101
1.4696
1.4483
0.6329
2.1951
1.6992
1.0811
1.1184
1.7626
1.4179
1.1310
1.6988
2.0949
1.6867
1.5203
1.2162
1.4231
1.1020
1.8868
1.4462
1.5901
1.6000
2.2018
1.4789
0.7767
1.5625
0.9957
1.3109
J-19
Draft November 12, 2004
-------
Year Species
Mean total length, cm Mean total weight, Kg
Se, ug/g dry wt.
80 Common carp
80 Common carp
80 Channel catfish
17
12
22.7
1.6667
1.4583
1.2551
78
78
Common carp
Striped mullet
Station 115, Colorado River at Yuma, Ariz.- Winterhaven, Calif.
16 2.7
20.3
3.4
6.4815
3.5958
White sucker
Northern pike
White sucker
White sucker
Station 116, Souris River at Upham, N. Dak.
16.5 2.3
19.6 1.9
15.3 1.7
13.8 1.3
78
80
80
80
Northern squawfish
Largescale sucker
Largescale sucker
Northern squawfish
Station 117, Flathead River at Creston, Mont.
19.1 2.7
15.4 1.3
15.5 1.3
15.8 1.3
0.7925
0.7589
0.9237
0.9091
Average
Std
max
min
count
J-20
Draft November 12, 2004
-------
Table J-2. Selenium concentration (ug/g dw whole-body) in fish and invertebrate samples collected at sites
of the USGS National Water Quality Assessment (NAWQA) Program, 1992-1997.
[Se] Scientific Name
0.30 Odonata
0.30 Hydropsyche
0.30 Hydropsyche
0.40 Odonata
0.40 Odonata
0.40 Corbicula
0.50 Pacifastacus leniusculus
0.50 Odonata
0.50 Odonata
0.50 Micropterus salmoides
0.60 Hydropsyche
0.60 Pacifastacus leniusculus
0.60 Hydropsyche
0.60 Potamogeton pectinatus
0.69 Tilapia melanotheron
0.70 Hydropsyche
0.70 Cottus sp.
0.70 Cheumatopsyche
0.70 Hydropsyche
0.80 Hydropsyche
0.90 Catostomusclarki
0.90 Odonata
0.90 Corbicula
0.90 Hydropsychidae
1.00 Hydropsyche
1.00 Cottus sp.
1.00 Orconectes
1.00 Hydropsyche
1.08 Poecilia sphenops
1.10 Acroneuria
1.10 Pacifastacus leniusculus
1.10 Pacifastacus leniusculus
1.10 Cottus sp.
1.10 Cottus sp.
1.10 Cottus sp.
1.10 Hydropsyche
1.10 Hydropsyche
1.10 Hydropsyche
1.15 Cheumatopsyche
1.20 Cyprinella lutrensis
1.20 Orconectes causeyi
1.20 Catostomus occidentalis
1.20 Xiphophorus helleri
1.20 Hydropsyche
1.20 Hydropsyche
1.20 Cottus sp.
Common Name
signal crayfish
largemouth bass
signal crayfish
sago pondweed
blackchin tilapia
freshwater sculpins
desert sucker
net-spinning caddisflies
freshwater sculpins
black molly
signal crayfish
signal crayfish
freshwater sculpins
freshwater sculpins
freshwater sculpins
red shiner
Sacramento sucker
green swordtail
freshwater sculpins
Place Name
GOOSE LAKE WMA
SF PALOUSE R. AT ARMSTRONG RD NR PULLMAN, WA
PALOUSE R. AT ENDICOTT-ST. JOHN RD NR COLFAX, WA
JOHNSONWPA
WOODDUCKWMA
SALUDA RIVER NEAR COLUMBIA, SC
TRUCKEE R AT FARAD, CA
DEPARTMENT OF ROADS - ONEILL
TODD VALLEY - MEDUNA SITE
TRINITY RV BL DALLAS, TX
ROCK CREEK BLW US HWY 30/93 AT TWIN FALLS ID
TRUCKEE R AT CLARK, NV
WOLF RIVER AT TURTLE LAKE ROAD AT POST LAKE, Wl
NORTH BRANCH MILWAUKEE RIVER NR RANDOM LAKE, Wl
ALA WAI CANAL AT HONOLULU, HI
CRAB CREEK AT MORGAN LAKE ROAD NEAR OTHELLO, WA
MILLER CREEK NEAR DES MOINES, WA
WOLF RIVER NEAR POST LAKE, Wl
WOLF RIVER NEAR POST LAKE, Wl
PESHEKEE RIVER NEAR MARTINS LANDING, Ml
PINTO CREEK NEAR MIAMI, AZ.
SABATKA SALINE WETLAND
SYCAMORE CKAT SYCAMORE PK, FT WORTH, TX
WOLF RIVER AT HIGHWAY M NEAR LANGLADE, Wl
SNAKE RIVER AT KING HILL ID
BIG SOOS CREEK ABOVE HATCHERY NEAR AUBURN, WA
EAST RIVER AT MIDWAY ROAD NEAR DE PERE, Wl
PENSAUKEE RIVER NEAR KRAKOW, Wl
KANEOHE STR BLW KAMEHAMEHA HWY, OAHU, HI
WEST BRANCH WHITEFISH RIVER NEAR DIFFIN, Ml
EAST FORK CARSON RIVER NEAR GARDNERVILLE, NV
EAST FORK CARSON RIVER NEAR DRESSLERVILLE, NV
SANDY RIVER NEAR TROUTDALE, OR
GALES CREEK NEAR GLENWOOD, OR
GALES CREEK NEAR GLENWOOD, OR
PALOUSE RIVER AT HOOPER, WA
SNAKE RIVER AB JACKSON LAKE AT FLAGG RANCH WY
SNAKE RIVER AB JACKSON LAKE AT FLAGG RANCH WY
DUCK CREEK AT SEMINARY ROAD NEAR ONEIDA, Wl
GRANITE CREEK AT PRESCOTT, AZ.
GRANITE CREEK AT PRESCOTT, AZ.
COTTONWOOD C NR COTTONWOOD CA
WAIHEE STR NR KAHALUU, OAHU, HI
HENRYS FORK NR REXBURG ID
ROCK CREEK AB HWY 30/93 XING AT TWIN FALLS ID
TUALATIN RIVER AT WEST LINN, OR
J-21
Draft November 12, 2004
-------
[Se] Scientific Name
1.20 Cottus sp.
1.20 Cottus sp.
1.20 Cottus sp.
1.20 Cheumatopsyche
1.20 Hydropsyche
1.30 Pacifastacus leniusculus
1.30 Cottidae
1.30 Micropterus salmoides
1.30 Cottus sp.
1.30 Hydropsyche
1.39 Cottus cognatus
1.40 Hydropsyche
1.40 Odonata
1.40 Pacifastacus leniusculus
1.40 Cottus sp.
1.40 Cottus sp.
1.40 Cottus sp.
1.40 Cottus sp.
1.40 Cheumatopsyche
1.40 Hydropsyche
1.50 Catostomusclarki
1.50 Hydropsyche
1.50 Brachycentrus
1.50 Odonata
1.50 Pacifastacus leniusculus
1.50 Pacifastacus leniusculus
1.50 Cottidae
1.50 Hydropsyche
1.50 Cottus sp.
1.50 Hydropsyche
1.50 Hydropsyche
1.50 Hydropsyche
1.53 Cyprinus carpio
1.60 Catostomusclarki
1.60 Hydropsyche
1.60 Cottidae
1.60 Elliptic
1.60 Hydropsyche
1.62 Corbicula
1.70 Hydropsyche
1.70 Hydropsyche
1.70 Corbicula
1.70 Elliptic
1.70 Corbicula
1.70 Hydropsyche
1.79 Cottidae
1.80 Hydropsychidae
1.80 Hydropsyche
1.80 Hydropsyche
1.90 Corbicula manilensis
1.90 Hydropsyche
1.90 Brachycentrus
1.90 Hydropsyche
1.95 Poecilia sphenops
2.00 Hydropsyche
2.00 Acroneuria
2.00 Cheumatopsyche
Common Name
freshwater sculpins
freshwater sculpins
freshwater sculpins
signal crayfish
sculpins
largemouth bass
freshwater sculpins
slimy sculpin
signal crayfish
freshwater sculpins
freshwater sculpins
freshwater sculpins
freshwater sculpins
desert sucker
signal crayfish
signal crayfish
sculpins
freshwater sculpins
Place Name
DENNIS C BL BLACK BUTTE MINE, NR COTTAGE GROVE LK
WEST BRANCH KELSEY CREEK AT BELLEVUE, WA
BERTRAND CREEK NEAR LYNDEN, WA
TOMORROW RIVER NEAR NELSONVILLE, Wl
SNAKE RIVER AB JACKSON LAKE AT FLAGG RANCH WY
TRUCKEE R AT FARAD, CA
JOHNSON CREEK AT MILWAUKIE, OR
WHITE ROCK LK IN DALLAS, TX
DUWAMISH RIVER AT GOLF COURSE AT TUKWILA, WA
DUCK CREEK AT SEMINARY ROAD NEAR ONEIDA, Wl
NINILCHIK R AT NINILCHIK AK
PORTNEUF RIVER AT POCATELLO ID
TRUST - WILD ROSE SLOUGH
TRUCKEE R AT HWY 447 AT NIXON, NV
MARYS RIVER AT CORVALLIS, OR
FIR CREEK NEAR BRIGHTWOOD, OR
FANNO CREEKAT DURHAM, OR
FANNO CREEKAT DURHAM, OR
DUCK CREEKAT SEMINARY ROAD NEAR ONEIDA, Wl
NORTH BRANCH MILWAUKEE RIVER NR RANDOM LAKE, Wl
SAN PEDRO RIVER AT CHARLESTON, AZ.
ROCK CREEK AB DAYDREAM RANCH NRTWIN FALLS ID
ROCK CREEK AB HWY 30/93 XING AT TWIN FALLS ID
TRUST - MORMON ISLAND CRANE MEADOW, EAST SLOUGH
CARSON RIVER AT DEER RUN ROAD NEAR CARSON CITY, NV
CARSON RIVER NEAR FORT CHURCHILL, NV
MUDDY CREEK NEAR PEORIA, OR
PALOUSE RIVER NEAR COLFAX, WA
THORNTON CREEK NEAR SEATTLE, WA
TOMORROW RIVER NEAR NELSONVILLE, Wl
SALT RIVER AB RESERVOIR NR ETNA WY
SALT RIVER AB RESERVOIR NR ETNA WY
common carp BEAR RIVER NEAR CORINNE, UT
desert sucker GILA RIVER AT KELVIN, AZ.
BARK RIVER NEAR BARK RIVER, Ml
sculpins FANNO CREEKAT DURHAM, OR
CEDAR CREEK BELOW MYERS CREEK NR HOPKINS, SC
PINE CREEKAT PINE CITY ROAD AT PINE CITY, WA
TRUCKEE R AT CLARK, NV
PORTNEUF RIVER AT TOPAZ ID
SNAKE RIVER AT KING HILL ID
TRENT RIVER NEAR TRENTON, NC
MCTIER CREEK (RD 209) NEAR MONETTA, SC
GILLSCREEKNEARHOPKINS.SC
SHEBOYGAN RIVER AT DOTYVILLE, Wl
sculpins LITTLE ABIQUA CREEK NEAR SCOTTS MILLS, OR
net-spinning caddisflies TRUCKEE R AT FARAD, CA
TETON RIVER NR ST ANTHONY ID
SNAKE R NR MINIDOKA ID (AT HOWELLS FERRY)
asian clam CHATTAHOOCHEE R AT SR 253 NEAR CHATTAHOOCHEE, FL
PALOUSE RIVER AT LAIRD PARK NR HARVARD, ID
ROCK CREEK AB HWY 30/93 XING AT TWIN FALLS ID
DUCK CREEKAT SEMINARY ROAD NEAR ONEIDA, Wl
black molly NUUANU STR ABV WAOLANI ST. AT HONOLULU, OAHU, HI
SPRING CREEKAT SHEEPSKIN RD NR FORT HALL ID
PESHEKEE RIVER NEAR MARTINS LANDING, Ml
DUCK CREEKAT SEMINARY ROAD NEAR ONEIDA, Wl
J-22
Draft November 12, 2004
-------
[Se] Scientific Name
2.03 Ameiurus natalis
2.05 Richardsonius balteatus
2.10 Catostomusclarki
2.10 Hydropsyche
2.10 Hydropsyche
2.10 Hydropsyche
2.10 Pacifastacus leniusculus
2.10 Hydropsyche
2.10 Hydropsyche
2.10 Cottussp.
2.17 Corbicula fluminea
2.18 Corbicula
2.20 Brachycentrus
2.20 Hydropsyche
2.20 Cottus sp.
2.20 Ceratopsyche
2.20 Brachycentrus
2.30 Agosia chrysogaster
2.30 Catostomusclarki
2.30 Hydropsyche
2.37 Ameiurus natalis
2.40 Xiphophorus helleri
2.40 Hydropsyche
2.40 Corbicula
2.40 Corbicula
2.40 Cottus sp.
2.40 Cottus sp.
2.50 Agosia chrysogaster
2.50 Hydropsyche
2.50 Hydropsyche
2.50 Anaspidacea
2.50 Elliptic
2.50 Corbicula
2.52 Xiphophorus helleri
2.60 Cottus sp.
2.60 Elliptic
2.60 Corbicula
2.60 Corbicula
2.60 Cottus sp.
2.64 Cyprinus carpio
2.70 Corbicula
2.70 Corbicula
2.70 Corbicula
2.70 Cottus sp.
2.70 Cottus sp.
2.70 Cottus sp.
2.77 Gambusia affinis
2.79 Cottus sp.
2.80 Corbicula manilensis
2.80 Corbicula
2.80 Decapoda
2.80 Corbicula
2.80 Brachycentrus
2.80 Hydropsyche
2.80 Hydropsyche
2.80 Hydropsyche
2.81 Salvelinus fontinalis
Common Name
yellow bullhead
redside shiner
desert sucker
-
signal crayfish
-
-
freshwater sculpins
Asian clam
-
-
freshwater sculpins
-
longfin dace
desert sucker
-
yellow bullhead
green swordtail
-
-
-
freshwater sculpins
freshwater sculpins
longfin dace
-
-
-
-
-
green swordtail
freshwater sculpins
-
-
freshwater sculpins
common carp
-
-
-
freshwater sculpins
freshwater sculpins
freshwater sculpins
western mosquitofish
freshwater sculpins
asian clam
-
crabs
-
-
-
brook trout
Place Name
SANTA ANA R A HAMNER RD NR NORCO CA
BEAR RIVER ABOVE RESERVOIR, NEAR WOODRUFF, UT
VERDE RIVER ABV W. CLEAR CREEK, NR CAMP VERDE, AZ
SNAKE R NR MINIDOKA ID (AT HOWELLS FERRY)
ROCK CK AT USFS FOOTBRIDGE, NR ROCK CREEK
ROCK CREEK AB HWY 30/93 XING AT TWIN FALLS ID
TRUCKEE R AT LOCKWOOD, NV
TUALATIN RIVER AT WEST LINN, OR
ESQUATZEL COULEE AT MESA, WA
FISHTRAP CREEK AT FLYNN ROAD AT LYNDEN, WA
CONTENTNEA CREEKAT HOOKERTON, NC
TENNESSEE RIVER AT CHATTANOOGA, TN
BITCH CREEK NR LAMONT ID
SOUTH BRANCH PAINT RIVER NEAR ELMWOOD, Ml
LITTLE ABIQUA CREEK NEAR SCOTTS MILLS, OR
EAST RIVER @ CTH PP IN BROWN COUNTY NR DE PERE, Wl
SALT RIVERV NR FISH CK ABOVE SMOOT
SANTA CRUZ RIVER AT TUBAC, AZ.
WEST CLEAR CREEK NEAR CAMP VERDE, AZ.
PORTNEUF RIVER AT TOPAZ ID
SANTA ANA R A MWD CROSSING CA
WAIKELESTRATWAIPAHU, OAHU, HI
MALAD RIVER NR GOODING ID
CRABTREE CREEKAT US 1 AT RALEIGH, NC
BLACKWATER RIVER NEAR FRANKLIN, VA
ROCK CREEKAT CEDAR FALLS ROAD NEAR LANDSBURG, WA
JUANITA CREEK AT JUANITA, WA
SALT RIVER NEAR ROOSEVELT, AZ.
SNAKE RIVER NR BLACKFOOT ID
SNAKE RIVER NR BLACKFOOT ID
EAST FORK CARSON RIVER NEAR GARDNERVILLE, NV
COOSAWHATCHIE RIVER NR EARLY BRANCH, SC
TAYLOR FLAT CREEK ABV BIRCH RD NR PASCO, WA
MANOASTRATKANEWAI FIELD, HONOLULU, OAHU, HI
PALMER C AT DAYTON, OR
SHAWS CREEK NR TRENTON, SC ON CNTY RD 149
PIGEON RIVER AT NEWPORT, TN
RUSH CKAT WOODLAND PARK BLVD, ARLINGTON, TX
NEWAUKUM CREEK NEAR BLACK DIAMOND, WA
SAN JACINTO R NR ELSINORE CA
EMORY RIVER AT OAKDALE, TN
GUADALUPE RV AT GONZALES, TX
NORTH MEHERRIN RIVER NEAR LUNENBURG, VA
GREEN RIVER ABOVE TWIN CAMP CREEK NEAR LESTER, WA
LEACH CREEK NEAR STEILACOOM, WA
NORTH CREEK BELOW PENNY CREEK NEAR BOTHELL, WA
MANOASTRATKANEWAI FIELD, HONOLULU, OAHU, HI
WEBER RIVER NEAR COALVILLE, UT
MUCKALEE CREEKAT GA 195, NEAR LEESBURG, GA
TAR RIVER NEAR TAR RIVER, NC
PLATTE RIVER AT BRADY, NE (TOTFLO)
COPPER CREEK NEAR GATE CITY, VA
SECOND SOUTH BRANCH OCONTO RIVER NR MOUNTAIN, Wl
TOMORROW RIVER NEAR NELSONVILLE, Wl
NORTH BRANCH MILWAUKEE RIVER NR RANDOM LAKE, Wl
SNAKE RIVER AB JACKSON LAKE AT FLAGG RANCH WY
WOOD RIVER ABOVE MIDDLE FORK NEAR MEETEETSE, WY
J-23
Draft November 12, 2004
-------
[Se] Scientific Name
2.85 Cottus cognatus
2.88 Salvelinus fontinalis
2.90 Corbicula manilensis
2.90 Corbicula manilensis
2.90 Corbicula manilensis
2.90 Corbicula manilensis
2.90 Corbicula manilensis
2.90 Corbicula manilensis
2.90 Hydropsyche
2.90 Corbicula
2.96 Cottus cognatus
2.96 Gambusia affinis
3.00 Cottus cognatus
3.00 Hydropsyche
3.00 Brachycentrus
3.00 Corbicula fluminea
3.00 Corbicula
3.00 Corbicula
3.00 Corbicula
3.10 Perlidae
3.10 Corbicula
3.10 Corbicula
3.10 Corbicula
3.18 Corbicula manilensis
3.20 Corbicula manilensis
3.20 Corbicula
3.20 Corbicula
3.30 Corbicula manilensis
3.30 Corbicula
3.30 Decapoda
3.30 Corbicula
3.40 Corbicula fluminea
3.40 Ceratopsyche
3.40 Cheumatopsyche
3.40 Corbicula
3.40 Hydropsyche
3.40 Hydropsyche
3.50 Corbicula manilensis
3.50 Corbicula manilensis
3.50 Corbicula
3.50 Corbicula fluminea
3.50 Corbicula
3.50 Corbicula
3.50 Corbicula
3.60 Cyprinella lutrensis
3.60 Agosia chrysogaster
3.60 Carpiodes carpio
3.60 Corbicula
3.60 Corbicula manilensis
3.60 Corbicula manilensis
3.60 Corbicula
3.60 Corbicula
3.60 Corbicula
3.60 Hydropsyche
3.60 Cottus sp.
3.60 Cottus sp.
Common Name
slimy sculpin
brook trout
asian clam
asian clam
asian clam
asian clam
asian clam
asian clam
slimy sculpin
western mosquitofish
slimy sculpin
Asian clam
common stoneflies
asian clam
asian clam
asian clam
crabs
Asian clam
asian clam
asian clam
Asian clam
red shiner
longfin dace
river carpsucker
asian clam
asian clam
freshwater sculpins
freshwater sculpins
Place Name
KENAI R AT JIMS LANDING NR COOPER LANDING AK
CROW CREEK AT MOUTH, AT PAHASKA, WY
APALACHICOLA RIVER AT CHATTAHOOCHEE FLA
FLINT RIVER AT NEWTON, GA
ICHAWAYNOCHAWAY CREEK BELOW NEWTON, GA
PEACHTREE CREEK AT ATLANTA, GA
FLINT RIVER AT LAKE BLACKSHEAR NEAR WARWICK, GA.
CHATTAHOOCHEE RIVER AT COLUMBUS, GA
SNAKE RIVER AT KING HILL ID
TRUCKEE R AT CLARK, NV
CHESTER C AT ARCTIC BOULEVARD AT ANCHORAGE AK
KANEOHE STR BLW KAMEHAMEHA HWY, OAHU, HI
KENAI R BL RUSSIAN R NR COOPER LANDING AK
PORTNEUF RIVER AT TOPAZ ID
TETON RIVER AB SOUTH LEIGH CREEK NR DRIGGS ID
BIG BLUE RIVER AT SHELBYVILLE, IN
TAR RIVER AT TARBORO, NC
NORTH FLAT RIVER AT TIMBERLAKE, NC
GILLS CREEK AT COLUMBIA, SC
BIG WOOD RIVER BLW BOULDER CK NR KETCHUM
NEUSE RIVER NEAR COX MILL, NC
SOUTH FORK CATAWBA RIVER AT MCADENVILLE, NC
INDIAN CREEK NEAR LABORATORY, NC
SNAKE CREEK NEAR WHITESBURG, GA
SPRING CREEK NEAR IRON CITY, GA.
ROANOKE RIVER AT ROANOKE RAPIDS, NC
NOTTOWAY RIVER NEAR SEBRELL, VA
BULL CREEK AT US 27 AT COLUMBUS, GEORGIA
CONOCOCHEAGUE CREEKAT FAIRVIEW, MD
WOOD RIVER NEAR GRAND ISLAND NEBR
NOLICHUCKY RIVER NEAR LOWLAND
SUGAR CREEKAT CO RD 400 S AT NEW PALESTINE, IN
WEST BRANCH WHITEFISH RIVER NEAR DIFFIN, Ml
JOHNSON CREEKAT MILWAUKIE, OR
POWELL RIVER NEAR ARTHUR, TN
PARADISE CREEKAT PULLMAN, WA
SALT RIVER AB RESERVOIR NR ETNA WY
FLINT R @ 10-MI STILL LANDING NR CHATTAHOOCHEE, FL
PEACHTREE CREEKAT ATLANTA, GA
NEUSE RIVER AT KINSTON, NC
NEUSE RIVER AT KINSTON, NC
SANTEE R AT TREZESVANTS LANDING NR FT MOTTE, SC
NOLICHUCKY RIVER AT EMBREEVILLE, TN
SAN MARCOS RV ABV BLANCO RV BL SAN MARCOS, TX
SALT RIVER NEAR ROOSEVELT, AZ.
AGUA FRIA RIVER NEAR ROCK SPRINGS, AZ.
BUCKEYE CANAL NR HASSAYAMPA
48TH STREET DRAIN NR INTERSTATE 10
APALACHICOLA RIVER NR BLOUNTSTOWN,FLORIDA
CHATTAHOOCHEE R AT SR 369 NR FLOWERY BRANCH, GA.
SWIFT CREEK AT HILLIARDSTON, NC
CHICOD CR AT SR1760 NEAR SIMPSON, NC
LITTLE RIVER NEAR MARYVILLE, TN
CRAB CREEKAT ROCKY FORD ROAD NEAR RITZVILLE, WA
ROCK CREEK NEAR MAPLE VALLEY, WA
NOOKSACK RIVER AT BRENNAN, WA
J-24
Draft November 12, 2004
-------
[Se] Scientific Name
3.66 Corbicula
3.70 Corbicula manilensis
3.70 Hydropsyche
3.70 Corbicula fluminea
3.70 Corbicula manilensis
3.77 Corbicula
3.80 Corbicula manilensis
3.80 Corbicula
3.80 Cottus sp.
3.80 Corbicula
3.85 Corbicula manilensis
3.90 Corbicula manilensis
3.90 Corbicula manilensis
4.00 Elliptic
4.00 Corbicula
4.01 Cyprinus carpio
4.10 Corbicula manilensis
4.10 Hydropsyche
4.10 Corbicula
4.10 Corbicula
4.10 Corbicula
4.16 Corbicula
4.20 Corbicula manilensis
4.20 Arctopsyche
4.20 Corbicula
4.20 Corbicula
4.30 Agosia chrysogaster
4.30 Corbicula manilensis
4.30 Corbicula manilensis
4.30 Elliptic
4.30 Corbicula
4.40 Cottus cognatus
4.40 Corbicula manilensis
4.40 Corbicula manilensis
4.40 Corbicula manilensis
4.40 Corbicula fluminea
4.40 Pacifastacus leniusculus
4.47 Corbicula manilensis
4.50 Agosia chrysogaster
4.50 Corbicula manilensis
4.50 Arctopsyche
4.50 Corbicula fluminea
4.50 Corbicula
4.50 Corbicula
4.57 Corbicula
4.60 Corbicula manilensis
4.60 Corbicula
4.60 Corbicula
4.64 Corbicula
4.76 Catostomus commersoni
4.80 Agosia chrysogaster
4.80 Corbicula manilensis
4.80 Corbicula
4.80 Cottus sp.
4.80 Cottus sp.
4.81 Corbicula
4.86 Cottus cognatus
5.09 Corbicula
Common Name
-
asian clam
-
Asian clam
asian clam
-
asian clam
-
freshwater sculpins
-
asian clam
asian clam
asian clam
-
-
common carp
asian clam
-
-
-
-
-
asian clam
-
-
-
longfin dace
asian clam
asian clam
-
-
slimy sculpin
asian clam
asian clam
asian clam
Asian clam
signal crayfish
asian clam
longfin dace
asian clam
-
Asian clam
-
-
-
asian clam
-
-
-
white sucker
longfin dace
asian clam
-
freshwater sculpins
freshwater sculpins
-
slimy sculpin
-
Place Name
CONGAREE RIVER AT COLUMBIA, SC
KINCHAFOONEE CREEK NEAR DAWSON, GA
BLACKFOOT RIVER AB RESERVOIR NR HENRY ID
WHITE RIVER AT RAYMOND STREET AT INDIANAPOLIS, IN
CURRENT RIVER AT VAN BUREN, MO
HOLSTON RIVER AT SURGOINSVILLE, TN
APALACHICOLA RIVER NR SUMATRA.FLA.
SWIFT CREEK NEAR APEX, NC
LUCKIAMUTE RIVER NEAR SUVER, OR
CATOCTIN CREEK AT TAYLORSTOWN, VA
SOPE CREEK NEAR MARIETTA, GA
NICKAJACK CR AT COOPER LAKE DR NR MABLETON, GA.
CHATTAHOOCHEE RIVER NEAR COLUMBIA, ALA.
GEORGES CREEK NEAR OLAR, SC ON SC 64
WATEREE RIVER NR. CAMDEN, SC
LEON CK AT IH 35 AT SAN ANTONIO, TX
WILLED CREEK AT ST RT 120 NEAR ROSWELL, GA.
MALAD RIVER NR GOODING ID
CARSON RIVER AT TARZYN ROAD NR FALLON, NV
FRENCH BROAD RIVER NEAR NEWPORT, TN
MIDDLE FORK HOLSTON RIVER AT SEVEN MILE FORD, VA
OBED RIVER NEAR LANCING, TN
SEWELL MILL CR AT SEWELL MILL RD NEAR MARIETTA
BIG LOST RIVER AT HOWELL RANCH NR CHILLY ID
CONGAREE RIVER AT U.S. HWY 601 NR. FORT MOTTE, SC
GUADALUPE RV NR SPRING BRANCH, TX
GILA RIVER AT KELVIN, AZ.
SOPE CREEK NEAR MARIETTA, GA
AYCOCKS CREEK NEAR BOYKIN, GA.
COW CASTLE CREEK NEAR BOWMAN, SC
NORTH FORK HOLSTON RIVER NEAR CLOUD FORD, TN
TALKEETNA R NR TALKEETNA AK
COOLEEWAHEE CREEK NEAR NEWTON, GA.
SOPE CREEK NEAR MARIETTA, GA
FLINT RIVER NEAR CULLODEN, GA
CLIFTY CREEKAT HARTSVILLE, IN
CARSON RIVER NEAR FORT CHURCHILL, NV
CHATTAHOOCHEE RIVER NEAR WHITESBURG, GA
SAN PEDRO RIVER AT CHARLESTON, AZ.
CHATTAHOOCHEE RIVER NEAR NORCROSS, GA
BIG LOST RIVER AT HOWELL RANCH NR CHILLY ID
LOST RIVER NEAR LEIPSIC, IN
CLINCH RIVER ABOVE TAZEWELL, TN
ESQUATZEL COULEE AT SAGEMOOR RD NEAR PASCO, WA
CHAMBERS CK NR RICE, TX
FLAT SHOAL CREEKAT STOVALL RD NEAR STOVALL, GA
BIG LIMESTONE CREEK NEAR LIMESTONE, TN
SALADO CK AT LOOP 13 AT SAN ANTONIO, TX
CONGAREE RIVER AT COLUMBIA, SC
SADDLE RIVER AT RIDGEWOOD NJ
PINTO CREEK NEAR MIAMI, AZ.
SNAKE CREEK NEAR WHITESBURG, GA
BEAVER CREEK BELOW LIBERTY HILL, SC
NF SKOKOMISH R BL STAIRCASE RPDS NR HOODSPORT, WA
NOOKSACK RIVER AT NORTH CEDARVILLE, WA
NORTH FORK HOLSTON RIVER NEAR HAYTER GAP, VA
CHESTER C AT ARCTIC BOULEVARD AT ANCHORAGE AK
MENARD CK NR FUQUA, TX
J-25
Draft November 12, 2004
-------
5.10 Corbicula manilensis
[Se] Scientific Name
5.10 Corbicula fluminea
5.10 Corbicula fluminea
5.10 Cottussp.
5.13 Cottussp.
5.19 Cottus cognatus
5.20 Cyprinella lutrensis
5.20 Corbicula fluminea
5.20 Corbicula
5.30 Corbicula fluminea
5.30 Corbicula
5.40 Corbicula manilensis
5.40 Corbicula manilensis
5.40 Corbicula
5.40 Corbicula
5.40 Corbicula
5.70 Corbicula
5.70 Corbicula
5.78 Hemichromis
5.79 Corbicula
5.80 Corbicula manilensis
5.80 Corbicula
5.81 Cottus cognatus
6.00 Corbicula fluminea
6.00 Corbicula
6.00 Hydropsyche
6.20 Corbicula
6.30 Corbicula
6.35 Cottus cognatus
6.68 Cottus cognatus
6.70 Agosia chrysogaster
6.70 Agosia chrysogaster
6.70 Corbicula manilensis
6.70 Corbicula
7.00 Corbicula
7.30 Corbicula
7.70 Corbicula
8.10 Corbicula
8.40 Corbicula
8.47 Cottus cognatus
9.10 Corbicula
9.40 Cyprinella lutrensis
9.56 Cottus cognatus
9.83 Ictalurus punctatus
1 0.47 Cottus cognatus
12.83 Corbicula
14.40 Hydropsyche
22.37 Salmo trutta
asian clam
Common Name
Asian clam
Asian clam
freshwater sculpins
freshwater sculpins
slimy sculpin
red shiner
Asian clam
Asian clam
-
asian clam
asian clam
-
-
-
-
-
jewelfishes
-
asian clam
-
slimy sculpin
Asian clam
-
-
-
-
slimy sculpin
slimy sculpin
longfin dace
longfin dace
asian clam
-
-
-
-
-
-
slimy sculpin
-
red shiner
slimy sculpin
channel catfish
slimy sculpin
brown trout
LIME CREEK NEAR COBB, GA
Place Name
KESSINGER DITCH NEAR MONROE CITY, IN
SALT CREEK AT HOOSIER AVENUE AT OOLITIC, IN
SKOKOMISH RIVER NEAR POTLATCH, WA
BEAR RIVER BELOW SMITHS FORK, NEAR COKEVILLE, WY
KAMISHAK R NR KAMISHAKAK
AGUA FRIA RIVER NEAR ROCK SPRINGS, AZ.
SUGAR CREEK AT CO RD 400 S AT NEW PALESTINE, IN
SOUTH BRANCH POTOMAC RIVER NEAR SPRINGFIELD, WV
EAST FORK WHITE RIVER AT SHOALS, IN
EDISTO RIVER NEAR COTTAGEVILLE.SC
CHATTAHOOCHEE RIVER NEAR CORNELIA, GA
WEST FORK LITTLE RIVER NEAR GAINESVILLE, GA.
TRUCKEE R AT LOCKWOOD, NV
BRUSHY CREEK NEAR PELHAM, SC
BIG CREEK ABOVE SALUDA, SC
AHOSKIE CR NEAR POORTOWN, NC
CLINCH RIVER AT SPEERS FERRY, VA
POAMOHO STREAM NR WAIALUA, OAHU, HI
KNOB CREEK AT AUSTIN SPRINGS
FLINT RIVER NEAR LOVEJOY, GA
SABINAL RV NR SABINAL, TX
MOOSE CNR PALMER AK
MUSCATATUCK RIVER NEAR DEPUTY, IN
LICK CREEK NEAR HOLLAND MILL, TN
CHAFFEE CREEKAT NESHKORO, Wl
MEDINA RV AT LA COSTE, TX
INDIAN CREEKABOVE NEWBERRY, SC
SF CAMPBELL C NR ANCHORAGE AK
COSTELLO C AB CAMP C NR COLORADO AK
AGUA FRIA RIVER NEAR MAYER, AZ.
AGUA FRIA RIVER AT BLOODY BASIN ROAD
CHATTAHOOCHEE RIVER NEAR WHITESBURG, GA
BLANCO RVATWIMBERLEY, TX
LONG CREEK ON SPENCER MTN RD NR SPENCER MTN, NC
GUEST RIVER AT COEBURN, VA
FRIO RV AT CONCAN, TX
VERDE R BLW TANGLE CREEK, ABV HORSESHOE DAM, AZ.
COMAL RV AT NEW BRAUNFELS, TX
COSTELLO C NR COLORADO AK
NUECES RV BL UVALDE, TX
VERDE R BLW TANGLE CREEK, ABV HORSESHOE DAM, AZ.
CAMP C AT MOUTH NR COLORADO AK
SABINAL RV NR SABINAL, TX
COSTELLO C BL CAMP C NR COLORADO AK
GERONIMO CK AT HWY 90A NR SEGUIN, TX
GREEN CREEK NEAR PALMER, Ml
TONGUE RIVER NEAR DAYTON, WY
J-26
Draft November 12, 2004
-------
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