AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
TRIBUTYLTIN
CAS Registry Number (See Text)
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
Final March 1991
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NOTICES
This document has been reviewed by the Criteria and Standards Division, Office
of Water Regulations and Standards, U.S. Environmental Protection Agency, and
approved for publication.
Mention of trade names or commercial products does not constitute endorsement
or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
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FOREWORD
Section 304(a)(l) of the Clean Water Act of 1977 (P.L. 95-217) requires
the Administrator of the Environmental Protection Agency to publish water quality
criteria that accurately reflect the latest scientific knowledge on the kind and
extent of all identifiable effects on health and welfare that might be expected
from the presence of pollutants in any body of water, including ground water.
This document is a revision of proposed criteria based upon consideration of
comments received from other federal agencies, state agencies, special interest
groups, and individual scientists. Criteria contained in this document replace
any previously published EPA aquatic life criteria for the same pollutant(s).
The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a)(l) and section 303(c)(2). The term has a different
program impact in each section. In section 304, the term represents a
non-regulatory, scientific assessment of ecological effects. Criteria presented
in this document are such scientific assessments. If water quality criteria
associated with specific stream uses are adopted by a state as water quality
standards under section 303, they become enforceable maximum acceptable pollutant
concentrations in ambient waters within that state. Water quality criteria
adopted in state water quality standards could have the same numerical values
as criteria developed under section 304. However, in many situations states
might want to adjust water quality criteria developed under section 304 to
reflect local environmental conditions and human exposure patterns before
incorporation into water quality standards. It is not until their adoption as
part of state water quality standards that criteria become regulatory.
Guidance to assist states in the modification of criteria presented in
this document, in the development of water quality standards, and in other
water-related programs of this agency have been developed by EPA.
Martha G. Prothro
Director
Office of Water Regulations and Standards
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ACKNOWLEDGMENTS
Larry T. Brooke David J. Hansen
(freshwater author) (saltwater author)
University of Wisconsin-Superior Environmental Research Laboratory
Superior, Wisconsin Narragansett, Rhode Island
Robert Scott Carr
(saltwater author)
Battelle New England Laboratory
Duxbury, Massachusetts
Robert L. Spehar David J. Hansen
(document coordinator) (saltwater coordinator)
Environmental Research Laboratory Environmental Research Laboratory
Duluth, Minnesota Narragansett, Rhode Island
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CONTENTS
Page
Foreword iii
Acknowledgments iv
Tables vi
Text Tables vii
Introduction 1
Acute Toxicity to Aquatic Animals 5
Chronic Toxicity to Aquatic Animals 8
Toxicity to Aquatic Plants 11
Bioaccumulation 12
Other Data 13
Unused Data 25
Summary 28
National Criteria 29
Implementation 30
References 65
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TABLES
Page
1. Acute Toxicity of Tributyltin to Aquatic Animals 32
2. Chronic Toxicity of Tributyltin to Aquatic Animals 39
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 41
4. Toxicity of Tributyltin to Aquatic Plants 46
5. Bioaccumulation of Tributyltin by Aquatic Organisms 48
6. Other Data on Effects of Tributyltin on Aquatic Organisms 51
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TEXT TABLES
Page
1. Summary of available laboratory and field studies
relating the extent of imposex of female snails,
measured by relative penis size (volume female
penis + male penis - RPS) and the vas deferens
sequence index (VDS), as a function of tributyltin
concentration in water and dry tissue 17
2. Summary of laboratory and field data on the effects
of tributyltin on saltwater organisms at concentrations
less than the Final Chronic Value of 0.0485 /xg/L 22
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Introduction
Organotins are compounds consisting of one to four organic moieties
attached to a tin atom via carbon-tin covalent bonds. When there are fewer than
four carbon-tin bonds, the organotin compound will be a cation unless the
remaining valences of tin are occupied by an anion such as acetate, carbonate,
chloride, fluoride, hydroxide, oxide, or sulfide. Thus a species such as
tributyltin (TBT) is a cation whose formula is (C«H9)3Sn*. In sea water TBT
exists mainly as a mixture of the chloride, the hydroxide, the aquo complex, and
the carbonate complex (Laughlin et al. 1986a).
Several review papers have been written which cover the production, use,
chemistry, toxicity, fate and hazards of TBT in the aquatic environment (Clark
et al. 1988; Eisler 1989; Oceans 86 1986; Oceans 87 1987; WHO 1990). The
toxicities of organotin compounds are related to the number of organic moieties
bonded to the tin atom and to the number of carbon atoms in the organic moieties.
Toxicity to aquatic organisms generally increases as the number of organic
moieties increases from one to three and decreases with the incorporation of a
fourth, making triorganotins more toxic than other forms. Within the
triorganotins, toxicity increases as the number of carbon atoms in the organic
moiety increases from one to four, then decreases. Thus the organotin most toxic
to aquatic life is TBT (Hall and Pinkney 1985; Laughlin and Linden 1985; Laughlin
et al. 1985). TBTs inhibit Na* and K* ATPases and are ionophores controlling
/
exchange of Cl", Br", F" and other ions across cell membranes (Selwyn 1976).
Organotins are used in several manufacturing processes, for example, as
an anti-yellowing agent in clear plastics and as a catalyst in poly(vinyl
chloride) products (Piver 1973). One of the more extensive uses of organotins
is as biocides (fungicides, bactericides, insecticides) and as preservatives for
wood, textiles, paper, leather and electrical equipment. The use of TBT in
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antifouling paints on ships, boats, docks and cooling towers probably contributes
most significantly to direct release of organotins into the aquatic environment
(Clark et al. 1988; Hall and Pinkney 1985; Kinnetic Laboratory 1984).
The U.S. Navy (1984) proposed application of some paints containing TBT
to hulls of naval ships. Such paint formulations have been shown to be an
effective and relatively long-lived deterrent to adhesion of barnacles and other
fouling organisms. Encrustations of these organisms on ships' hulls reduce
maximum speed and increase fuel consumption. According to the U.S. Navy (1984),
use of TBT paints, relative to other antifouling paints, would not only reduce
fuel consumption by 15% but would also increase time between repainting from less
than 5 years to 5 to 7 years. Release of TBT to water occurs during repainting
in shipyards when old paint is sand-blasted off and new paint applied. TBT would
also be released continuously from the hulls of the painted ships. Antifouling
paints in current use contain copper as the primary biocide, whereas the proposed
TBT paints would contain both copper and TBT. Interaction between the toxicities
of TBT and other ingredients in the paint apparently is negligible (Davidson et
al. 1986a).
The solubility of TBT compounds in water is influenced by such factors as
the oxidation-reduction potential, pH, temperature, ionic strength, and
concentration and composition of the dissolved organic matter (Clark et al. 1988;
Corbin 1976) . The solubility of tributyltin oxide in water was reported to be
750 ug/L at pH of 6.6, 31,000 ug/L at pH of 8.1 and 30,000 ug/L at pH 2.6
(Maguire et al. 1983). The carbon-tin covalent bond does not hydrolyze in water
(Maguire et al. 1983,1984), and the half-life for photolysis due to sunlight is
greater than 89 days (Maguire et al. 1985; Seligman et al. 1986). Biodegradation
is the major breakdown pathway for TBT in water and sediments with half-lives
of several days in water to several weeks in sediments (Clark et al. 1988; Lee
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et al. 1987; Maguire and Tkacz 1985; Seligraan et al. 1986, 1988, 1989; Stang and
Seligman 1986). Breakdown products include di- and monobutyltins with some
butylmethyltins detected.
Some species of algae, bacteria, and fungi have been shown to degrade TBT
by sequential dealkylation, resulting in dibutyltin, then monobutyltin, and
finally inorganic tin (Barug 1981; Maguire et al. 1984). Barug (1981) observed
the biodegradation of TBT to di- and monobutyltin by bacteria and fungi only
under aerobic conditions and only when a secondary carbon source was supplied.
Inorganic tin can be methylated by estuarine microorganisms (Jackson et al.
1982). Maguire et al. (1984) reported that a 28-day culture of TBT with the
green alga, Ankistrodesmus falcatus. resulted in 7% inorganic tin. Maguire
(1986) reported that the half-life of TBT exposed to microbial degradation was
five months under aerobic conditions and 1.5 months under anaerobic conditions.
TBT is also accumulated and metabolized by Zostera marina (Francios et al. 1989) .
The major metabolite of TBT in saltwater crabs, fish, and shrimp was dibutyltin
(Lee 1986).
TBT readily sorbs to sediments and suspended solids and can persist there
(Cardarelli and Evans 1980). In some instances, most TBT in the water column
(70-90%) is associated with the dissolved phase (Valkirs et al. 1986a; Maguire
1986; Johnson et al. 1987). The half-life for desorption of TBT from sediments
is reported to be greater than ten months (Maguire and Tkacz 1985).
Elevated TBT concentrations in fresh and salt waters, sediments or biota,
are primarily associated with harbors and marinas (Cleary and Stebbing 1985; Hall
1988; Hall et al. 1986; Langston et al. 1987; Maguire 1984,1986; Maguire and
Tkacz 1985; Maguire et al. 1982; Quevauviller et al. 1989; Salazar and Salazar
1985b; Seligman et al. 1986,1989; Short and Sharp 1989; Stallard et al. 1986;
Stang and Seligman 1986; Unger et al. 1986; Valkirs et al. 1986b; Waldock and
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Miller 1983; Waldock et al. 1987). Lenihan et al. (1990) hypothesized that
changes in faunal composition in hard bottom communities in San Diego Bay were
related to boat mooring and TUT. Salazar and Salazar (1988) found an apparent
relationship between concentrations of TBT in waters of San Diego Bay and reduced
growth of mussels. Organotin concentrations in the low part per trillion range
have been associated with oyster shell malformations (Alzieu et al. 1989). In
some cases the water surface microlayer contained a much higher concentration
of TBT than the water column (Cleary and Stebbing 1987; Hall et al. 1986; Valkirs
et al. 1986a). Gucinski (1986) suggested that this enrichment of the surface
microlayer might increase the bioavallability of TBT. TBT accumulates in
sediments with sorption coefficients which may range from l.lxlO2 to 8.2xl03 L/Kg
and desorption appears to be a two step process (Unger et al. 1987,1988). No
organotins were detected in the muscle tissue of feral chinook salmon,
Oncorhynchus tshawytscha. caught near Auke Bay, Alaska, but concentrations as
high as 900 ug/kg were reported in muscle tissue of chinook salmon held in pens
.treated with TBT (Short 1987; Short and Thrower 1986a).
Only data generated in toxicity and bioconcentration tests on TBTC
(tributyltin chloride; CAS 1461-22-9), TBTF (tributyltin fluoride; CAS 1983-10-
4), TBTO [bis(tributyltin) oxide; CAS 56-35-9], commonly called "tributyltin
oxide" and TBTS [bis(tributyltin) sulfide; CAS 4808-30-4], commonly called
"tributyltin sulfide" were used in the derivation of the water quality criteria
concentrations for aquatic life presented herein. All concentrations from such
tests are expressed as TBT, not as tin and not as the chemical tested.
Therefore, many concentrations listed herein are not those in the reference cited
but are concentrations adjusted to TBT. A comprehension of the "Guidelines for
Deriving Numerical National Water Quality Criteria for the Protection of Aquatic
Organisms and Their Uses" (Stephan et al. 1985), hereinafter referred to as the
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Guidelines, and the response to public comment (U.S. EPA 1985a) is necessary to
understand the following text, tables, and calculations. Results of such
intermediate calculations as recalculated LC50s and Species Mean Acute Values
are given to four significant figures to prevent roundoff error in subsequent
calculations, not to reflect the precision of the value. The Guidelines requires
that all available pertinent laboratory and field information be used to derive
a criterion consistent with sound scientific evidence. The saltwater criterion
for TBT follows this requirement by using data from chronic exposures of copepods
and molluscs rather than Final Acute Values and Acute-Chronic Ratios to derive
the Final Chronic Value. The Federal Insecticide, Fungicide, and Rodenticide
Act (FIFRA) data base of information from the pesticide industry was searched
and some useful information was located for deriving the criteria. The latest
comprehensive literature search for information for this document was conducted
in November 1990, some newer information has been included.
Acute Toxicity to Aquatic Animals
Data that may be used, according to the Guidelines, in the derivation of
Final Acute Values for TBT are presented in Table 1. Acute values are available
for thirteen freshwater species representing twelve genera. The acute values
range from 1.14 ug/L for a hydra, Hydra oligactis. to 24,600 ug/L for a
freshwater calm, Elliptic complanatus. The relatively low sensitivity of the
freshwater clam to TBT is surprising due to the mollusicidal qualities of TBT.
The organism likely closes itself to the environment, minimizing chemical intake,
and is able to tolerate high concentrations of TBT temporarily.
The most sensitive freshwater organisms tested are hydras (Table 3). Three
species were tested and have Species Mean Acute Values (SMAVs) ranging from 1.14
to 1.80 ug/L. Other invertebrate species tested are an amphipod, a cladoceran,
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an annelid and a dipteran larvae. Brooke et al. (1986) conducted flow-through
measured tests with an amphipod, Gammarus pseudolimnaeus. and an annelid,
Lumbriculus variegatus. and a static measured test with larvae of a mosquito,
Culex sp. The 96-hr LCSOs and SMAVs are 3.7, 5.4 and 10.2 ug/L, respectively.
Five tests with the daphnid, Daphnia magna. were conducted. The 48-hr EC50 value
of 66.3 ug/L (Foster 1981) was considerably less sensitive than those from the
other tests which ranged from 1.58 ug/L (LeBlanc 1976) to 11.2 ug/L (ABC
Laboratories, Inc. 1990c) . The SMAV for D. magna is 4.3 ug/L because, according
to the Guidelines, when test results are available from flow-through and
concentration measured tests, these have precedence over other types of acute
tests.
All the vertebrate species tested are fish. The most sensitive species
is the fathead minnow, Pimephales promelas. which has a SMAV of 2.6 ug/L from
a single 96-hr flow-through measured test (Brooke et al. 1986). Rainbow trout,
Oncorhynchus mykiss. were tested by four groups with good agreement. The 96-hr
LCSOs ranged from 3.45 to 7.1 ug/L with a SMAV of 4.571 ug/L for the three tests
(Brooke et al. 1986; ABC Laboratories, Inc. 1990a) which were conducted flow-
through and concentrations were measured. Bluegill, Lepomis macrochirus. were
tested by three groups. The value of 227.4 ug/L (Foster 1981) appears high
compared to those of 7.2 ug/L (Buccafusco 1976b) and 8.3 ug/L (ABC Laboratories,
Inc. 1990b). Only the flow-through measured test can be used, according to the
Guidelines, to calculate the SMAV of 8.3 ug/L.
Freshwater Genus mean Acute Values (GMAVs) are available for twelve genera
which vary by more than 21,000 times from the least sensitive to the most
sensitive. Removing the least sensitive genera, Elliptic. the remainder differ
from one another by a maximum factor of 8.7 times. Based upon the twelve
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available GMAVs the Final Acute Value (FAV) for freshwater organisms is 0.9177
ug/L. The FAV is lower than the lowest freshwater SMAV.
Tests of the acute toxicity of TBT to resident North American saltwater
species that are useful for deriving water quality criteria concentrations have
been performed with 20 species of invertebrates and six species of fish (Table
1). The range of acute toxicity to saltwater animals is a factor of about 670.
Acute values range from 0.42 ug/L for juveniles of the mysid, Acanthomysis
sculpta (Davidson et al. 1986a,1986b) to 282.2 ug/L for adult Pacific oysters,
Crassostrea gigas (Thain 1983). The 96-hr LCSOs for six saltwater fish species
range from 1.460 ug/L for juvenile chinook salmon, Oncorhynchus tshawytscha
(Short and Thrower 1986b) - to 25.9 ug/L for subadult sheepshead minnows,
Cyprinodon variegatus (Bushong et al. 1988).
Larval bivalve molluscs and juvenile crustaceans appear to be much more
sensitive than adults during acute exposures. The 96-hr LC50 for larval Pacific
oysters was 1.557 ug/L, whereas the value for adults was 282.2 ug/L (Thain 1983).
The 96-hr LCSOs for larval and adult blue mussels, Mytilus edulis. were 2.238
and 36.98 ug/L, respectively (Thain 1983). Juveniles of the crustaceans
Acanthomvsis sculpta and Metamysidopsis elongata were slightly more sensitive
to TBT than adults (Davidson et al. 1986a,1986b; Valkirs et al. 1985; Salazar
and Salazar, Manuscript).
Genus Mean Acute Values for 25 saltwater genera range from 0.61 ug/L for
Acanthomysis to 204.4 ug/L for Ostrea (Table 3). Genus Mean Acute Values for
the 11 most sensitive genera differ by a factor of less than four. Included
within these genera are three species of molluscs and eight species of
crustaceans. The saltwater Final Acute Value for TBT was calculated to be 0.7128
ug/L (Table 3), which is greater than the lowest saltwater Species Mean Acute
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Value of 0.61
Chronic Toxlcity to Aquatic Animals
The available data that are usable, according to the Guidelines, concerning
the chronic toxicity of TBT are presented in Table 2. Brooke et al. (1986)
conducted a 21-day life-cycle test with a freshwater cladoceran and reported that
the survival of adult Daphnia magna was 40% at a TBT concentration of 0.5 ug/L,
and 100% at 0.2 ug/L. The mean number of young per adult per reproductive day
was reduced 30% by 0.2 ug/L, and was reduced only 6% by 0.1 ug/L. The chronic
limits are 0.1 and 0.2 ug/L based upon the reproductive effects on adult
daphnids . The chronic value for Daphnia magna is calculated to be 0.1414 ug/L,
and the acute-chronic ratio of 30.41 is calculated using the acute value of 4 . 3
ug/L from the same study.
Daphnia magna were exposed in a second 21-day life -cycle test to TBT (ABC
Laboratories, Inc. 1990d) . Exposure concentrations ranged from 0.12 to 1.27 ug/L
as TBT. Survival of adults was significantly reduced (45%) from the controls
at >0.34 ug/L but not at 0.19 ug/L. Mean number of young per adult per
reproductive day was significantly reduced at the same concentrations affecting
survival. The chronic limits are set at 0.19 where no effects were seen and 0.34
ug/L where survival and reproduction were reduced. The Chronic Value is 0.2542
ug/L and the Acute -Chronic Ratio is 44.06 when calculated from the acute value
of 11.2 ug/L from the same test. The Acute-Chronic Ratio for D. magna is 36.60
which is the geometric mean of the two available Acute-Chronic ratios (30.41 and
44.06) for D. magna.
In an early life-stage test with the fathead minnow, Pimephales promelas .
all fish exposed to the highest exposure concentration of 2.20 ug/L died during
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the test (Brooke et al. 1986). Survival was reduced by 2% at the next lower TBT
concentration of 0.92 ug/L, but was higher than in the controls at 0.45 ug/L
and lower concentrations. The mean weight of the surviving fish was reduced 4%
at 0.08 ug/L, 9% at 0.15 ug/L, 26% at 0.45 ug/L, and 48% at 0.92 ug/L. Mean
length of fry at the end of the test was significantly reduced at concentrations
>0.45 ug/L. The mean biomass at the end of the test was higher at the lowest
TBT concentrations (0.08 and 0.15 ug/L) than in the controls, but was reduced
by 13 and 52% at TBT concentrations of 0.45 and 0.92 ug/L, respectively. Because
the reductions in weight were small at the two lowest concentrations (0.08 and
0.15 ug/L) and the mean biomass increased at these same concentrations, the
chronic limits are 0.15 and 0.45 ug/L based upon growth (length and weight).
Thus the chronic value is 0.2598 ug/L and the acute-chronic ratio is 10.01
calculated using the acute value of 2.6 ug/L from the same study.
Life-cycle toxicity tests have been conducted with the saltwater mysid,
Acanthomysis sculpta (Davidson et al. 1986a,1986b). The effects of TBT on
survival, growth, and reproduction of A. sculpta were determined in five separate
tests lasting from 28 to 63 days. The tests separately examined effects of TBT
on survival (1 test), growth (3 tests) and reproduction (1 test) instead of the
approach of examining all endpoints in one life-cycle test. All tests began with
newly released juveniles and lasted through maturation and spawning, therefore,
are treated as one life-cycle test. The number of juveniles released per female
at a TBT concentration of 0.19 ug/L was 50% of the number released in the control
treatment, whereas the number released at 0.09 ug/L was higher than in the
control treatment. Reductions in juveniles released resulted from deaths of
embryos within broad pouches of individual females and not from reduced
fecundity. Numbers of females releasing viable juveniles was reduced in 0.19
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and 0.33 /ig/L. At concentrations of 0.38 ug/L and above, survival and weight
of female mysids were always reduced; all mysids in 0.48 /Zg/L died. The chronic
value is 0.1308 ug/L, and the acute-chronic ratio is 4.664 (Table 2).
Two partial life-cycle toxicity tests were conducted using the copepod,
Eurytemora affinis (Hall et al. 1987;1988a). Tests began with egg-carrying
females and lasted 13 days. In the first test, mean brood size was reduced from
15.2 neonates/female in the control to 0.2 neonates/female in 0.479 ug/L.
Percentage survival of neonates relative to controls was 21% in 0.088 ug/L
(nominal concentration of 0.100 ug/L), and 0% in 0.479 ug/L. The chronic value
is <0.088 ug/L in this test. In the sec'ond test, percentage survival of neonates
was significantly reduced (27% relative to controls) in 0.224 ug/L; brood size
was unaffected in any tested concentration (0.018-0.224 ug/L). Although no
statistically significant effects were detected in <0.100 ug/L, percentage
survival of neonates appears reduced; 76% vs 90% in controls. The chronic value
in this test is 0.150 ug/L. Survival of neonates in both tests in the 0.100 ug/L
nominal concentration (mean measured concentration = 0.094 ug/L) averaged 42%
relative to controls. If this is the best estimate of the upper chronic value,
and the 0.056 /Ug/L treatment from the second test is the best estimate of the
lower chronic value, the overall chronic value for the two tests is 0.0725 ug/L.
The overall acute-chronic ratio is 27.24 when the acute value of 1.975 ug/L (mean
of acute values of 1.4, 2.2 and 2.5 ug/L) is used.
The Final Acute-Chronic Ratio of 14.69 was calculated as the geometric mean
of the acute-chronic ratios of 36.60 for Daphnia magna. 10.01 for Pimephales
promelas. 4.664 for Acanthomysis sculpta and 27.24 for Eurvtemora affinis.
Division of the freshwater and saltwater Final Acute Values by 14.69 results in
Final Chronic Values for freshwater of 0.0625 ug/L and for saltwater of 0.0485
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ug/L (Table 3). Both of these Chronic Values are below the experimentally
determined chronic values from life-cycle or early life-stage tests.
Toxicity to Aquatic Plants
Blanck et al. (1984) reported the concentrations of TBT that prevented
growth of thirteen freshwater algal species (Table 4) . These concentrations
ranged from 56.1 to 1,782 ug/L, but most were between 100 and 250 ug/L. No data
are available on the effects of TBT on freshwater vascular plants.
Toxicity tests on TBT have been conducted with five species of saltwater
phytoplankton including the green alga, Dunaliella tertiolecta: the diatoms,
Minutorellus polvmorphus. Nitzshic sp., Phaeodactylum tricornutum. Skeletonema
costatum. and Thallassiosira pseudonana: the dinoflagellate, Gymnodinium
splendens. the microalga, Pavlova lutheri and the macroalga, Fucus vesiculosus
(Tables 4 and 6). The 14-day EC50 of 0.06228 ug/L for S. costatum (EG&G
Bionomics 1981c) was the lowest value reported, but Thain (1983) reported that
a measured concentration of 0.9732 ug/L was algistatic to the same species (Table
4). The 72-hr ECSOs based on population growth ranged from approximately 0.3
to < 0.5 ug/L (Table 6). Lethal concentrations were generally more than an order
of magnitude greater than ECSOs and ranged from 10.24 to 13.82 ug/L. Identical
tests conducted on tributyltin acetate, tributyltin chloride, tributyltin
fluoride, and tributyltin oxide with £>. costatum resulted in ECSOs from 0.2346
to 0.4693 ug/L and LCSOs from 10.24 to 13.82 ug/L (Walsh et al. 1985).
A Final Plant Value, as defined in the Guidelines, cannot be obtained
because no test in which the concentrations of TBT were measured and the endpoint
was biologically important has been conducted with an important aquatic plant
species. The available data do indicate that freshwater and saltwater plants
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will be protected by TBT concentrations that adequately protect freshwater and
saltwater animals.
Bioaccumulation
Bioaccumulation of TBT has been measured in one species of freshwater fish
(Table 5). Martin et al. (1989) determined the whole body bioconcentration
factor (BCF) for rainbow trout to be 406 after a 64-day exposure to 0.513 /Ug
TBT/L. Equilibrium of the TBT concentration was achieved in the fish in 24 to
48 hrs. In a separate exposure to 1.026 /LlgTBT/L, rainbow trout organs were
assayed for TBT content after a 15-day exposure. The BCFs ranged from 312 for
muscle to 5,419 for peritoneal fat. TBT was more highly concentrated than the
metabolites of di- and monobutyltin or tin.
The extent to which TBT is accumulated by saltwater animals from the field
or from laboratory tests lasting 28 days or more has been investigated with
three species of bivalve molluscs and a snail (Table 5) . Thain and Waldock
(1985) reported a BCF of 6,833 for the soft parts of blue mussel spat exposed
to 0.24 ug/L for 45 days. In other laboratory exposures of blue mussesl, Salazar
and Salazar (1990a) observed BCFs of 10,400 to 37,500 after 56 to 60 days. BAFs
from field deployments of mussels were similar to BCFs from laboratory studies;
11,000 to 25,000 (Salazar and Salazar 1990a) and 5,000 to 60,000 (Salazar and
Salazar in press). Laboratory BCFs for the snail Nucella lepillis (11,000 to
38,000) were also similar to field BAFs (17,000) (Bryan et al. 1987). The soft
parts of the Pacific oyster exposed to TBT for 56 days contained 11,400 times
the exposure concentration of 0.146 ug/L (Waldock and Thain 1983). A BCF of
6,047 was observed for the soft parts of the Pacific oyster exposed to 0.1460
ug/L for 21 days (Waldock et al. 1983). The lowest steady-state BCF reported
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for a bivalve was 192.3 for the soft parts of the European flat oyster, Ostrea
edulis. exposed to a TBT concentration of 2.62 ug/L for 45 days (Thain 1986;
Thain and Waldock 1985).
No U.S. FDA action level or other maximum acceptable concentration in
tissue, as defined in the Guidelines, is available for TBT, and, therefore, no
Final Residue Value can be calculated.
Other Data
Additional data on the lethal and sublethal effects of TBT on aquatic
species are presented in Table 6. Wong et al. (1982) exposed a natural
assemblage of freshwater algae and several pure cultures of various algal species
to TBT in 4-hr exposures. Effects (EC50s) were seen in all cases on the
production or reproduction at concentrations ranging from 5 to 20 ug/L which
demonstrates a high sensitivity to TBT.
Larvae of the clam, Corbicula fluminea. has a 24-hr EC50 of 1,990 ug/L
which is a high concentration relative to most other species of tested freshwater
organisms. Another species of clam, Elliptic complanatus. also showed low
sensitivity to TBT with a 96-hr LC50 of 24,600 ug/L (Table 1). Various bivalve
clam species may have the ability to reduce exposure to TBT temporarily by
closing the valves.
The cladoceran, Daphnia magna. has 24-hr ECSOs ranging from 3 to 13.6 ug/L
(Bolster and Halacha 1972; Vighi and Calamari 1985). When a more sensitive
endpoint of altered phototaxis was examined in a longer-term exposure of 8 days,
the effect concentration (0.45 ug/L) was much lower (Meador 1986). Similarly,
rainbow trout (Oncorhynchus mykiss) exposed in short-term exposures of 24 to 48
hr have LC50 and EC50 values from 18.9 to 30.8 ug/L (Table 6). When the exposure
13
-------
is increased to 110 days, the LC100 decreased to 4.46 ug/L and a 10% reduction
in growth is seen at 0.18 ug/L. The frog, Rana temporaria. has a LC50 of 28.2
ug/L for a 5-day exposure to TBT.
An attempt was made to measure the bioconcentration of TBT with the green
alga, Ankistrodesmus falcatus (Maguire et al. 1984). The algae are able to
degrade TBT to its di- and monobutyl forms. As a result, the concentrations of
TBT steadily declined during the 28-day study. During the first seven days of
exposure, the concentrations declined from 20 to 5.2 ug/L and the calculated BCF
was 300 (Table 6). After 28 days of exposure, the TBT concentration had declined
to 1.5 ug/L and the calculated BCF was 467.
TBT has been shown to produce the superimposition of male sexual
characteristics on female neogastropod (stenoglossan) snails (Smith 1981b, Gibbs
and Bryan 1987). This phenomenon, termed "imposex," can result in females with
a penis, a duct leading to the vas deferens, and a convolution of the normally
straight oviduct (Smith 1981a). Other anatomical changes associated with imposex
are detailed in Gibbs et al. (1988) and Gibbs and Bryan (1987). Severity of
imposex is quantified using relative penis size (RPS; ratio of female to male
penis volume) and the six developmental stages of the vas deferens sequence (VDS)
(Bryan et al. 1986; Gibbs et al. 1987). TBT has been shown to impact populations
of the Atlantic dogwhinkle (dogwhelk), Nucella lapillus. which has direct
development. In neoglossian snails with indirect development through planktonic
larval stages, the impacts of TBT are less certain because recruitment is
facilitated. Natural pseudohemaphiodism in neoglossans occurs (Salazar and Champ
1988) and may be caused by other organotin compounds (Bryan et al. 1988a).
However, increased global incidence and severity of imposex has been associated
with areas of high boating activity and high concentrations of TBT in water,
14
-------
sediment or snails and other biota (Alvarez and Ellis 1990; Bailey and Davies
1988a,1988b; Bryan et al. 1986,1987,; Davies et al. 1987, Durchon 1982; Ellis
and Pattisima 1990; Gibbs and Bryan 1986,1987; Gibbs et al. 1987; Langston et
al. 1990; Short et al. 1989; Smith 1981a,1981b; Spence et al. 1990).
Although imposex has been observed in 45 species of snails worldwide (Ellis
and Pattisima 1990, Jenner 1979), definitive laboratory and field studies
implicating TBT as the cause have focused on three North American or cosmopolitan
species; the Atlantic dogwhinkle (Nucella lapillus). file dogwhinkle (N. lima)
and the eastern mud snail fIlyanassa (Nassarius) obsoletal. Imposex has been
associated with reduced reproductive potential and altered density and population
structure in field populations of N. lapillus (Spence et al. 1990). This is
related to blockage of the oviduct by the vas deferens, hence, prevention of
release of egg capsules, sterilization of the female or change into an apparently
fuctional male (Bryan et al. 1986; Gibbs et al. 1987,1988; Gibbs and Bryan
1986,1987). TBT may reduce populations of N. lima as snails were absent from
marinas in Auke Bay, AK. At intermediate distances from marinas, about 25 were
caught per hour of sampling and 250 per hour were caught at sites distant from
marinas (Short et al. 1989). Snails from intermediate sites had blocked
oviducts. Reduced proportions of female I_. obsoleta in Sarah Creek, VA also
suggests population impacts (Bryan et al. 1989). However, other causes may
explain this as oviducts were not blocked and indirect development facilitating
recruitment may limit impacts.
Several field studies have used transplantations of snails between sites
or snails painted with TBT paints to investigate the role of TBT or proximity
to marinas in the development of imposex without defining actual exposure
concentrations of TBT. Short et al. (1989) painted Nucellus lima with TBT-based
15
-------
paint, copper paints or unpainted controls. For 21 females painted with TBT
paint, seven developed penises within one month, whereas penises were absent from
35 females from other treatments. Smith (1981a) transplanted 1. obsoletus
between marinas and "clean" locations and found that incidence of imposex was
unchanged after 19 weeks in snails kept at clean locations or marinas, increased
in snails transplanted from clean sites to marinas and decreased somewhat in
transplants from marinas to clean sites. Snails exposed in the laboratory to
TBT-based paints in two separate experiments developed imposex within one month
with maximum impact within 6 to 12 months (Smith 1981a) . Snails painted with
non-TBT paints were unaffected.
Concentration-response data demonstrate a similarity in the response of
snails to TBT in controlled laboratory and field studies (Text Table 1) . Eastern
mud snails, Illyanassa obsoleta. collected from the York River, VA near Sarah
Creek had no incidence of imposex (Bryan et al. 1989) and contained no detectable
TBT, (<0.020 ug/g dry weight). The average TBT concentrations of York River
water was 0.0016 ug/L. In contrast, the average TBT concentrations from four
locations in Sarah Creek, VA were from 0.010 to 0.023 ug/L, snails contained
about 0.1 to 0.73 ug/g and there was a 40 to 100% incidence of imposex. Short
et al. (1989) collected file dogwinkle snails, Nucella lima, from Auke Bay, AK
and did not detect imposex or TBT in snails from sites far from marinas. Snails
from locations near marinas all exhibited imposex and contained 0.03 to 0.16
The effects of TBT on the development of imposex has been studied most in
the Atlantic dogwhinkle, Nucella lapillus. Bryan et al . 1987 exposed adult
snails for two years to 0.0036 (control), 0.0083, 0.046 and 0.26 ug/L in the
laboratory and compared responses to a field control. Imposex was present in
16
-------
Text Table 1. Summary of available laboratory and field studies relating the extent of Imposex
of female snails, measured by relative penis size (volume female penis+roale penis = RPS)
and the vas deferens sequence index (VDS), as a function of tributyltin
concentration in water and dry tissue
TBT Concentration
Species
Eastern mud snail ,
Ilyanassa obsoleta
File dogwhinkle,
Nucella lima
Atlantic dogwhinkle,
(adults),
Nucella lapillus
Atlantic dogwhinkle,
Nucella lapillus
Atlantic dogwhinkle,
(egg capsule to
adult),
Nucella lapillus
Atlantic dogwhinkle,
Nucella lapillus
Atlantic dogwhinkle,
Nucella lapillus
Atlantic dogwhinkle,
Nucella lapillus
capsules
Experimental
Desiqn
Field-York River
-Sarah Creek
Field-Auke Bay, AK
-Auke Bay, AK
Crooklets Beach, UK
Laboratory. 2 year
exposure
Laboratory, spires
painted, 8 mo.
Crooklets Beach, UK
Laboratory; 2 year
exposure
Transplants, Crooklets
Beach to Dart Estuary
Field, S.W. UK
S W. UK
Forth Joke, UK
Crooklets Beach, UK
Meadfoot. UK
Renney Rocks
Batten Bay
Water. ua/L
0.0016
0.01-0.023
.
-
<0.0012*
0.0036*
0.0083*
0.046*
0.26*
_
<0 0012
0.0036
0.0093
0.049
0.24
0.022-0.046
0.002-0 005*
-0.010
-0.017-0.025*
_
-
-
-
~
Snail
Tissue,
uq/q dry
<0 02
-0.1-0 73
N0(<0 01)
0 03-0 16
0 14-0 25*
0 41*
0 74*
4 5*
8 5*
-5 1*
0.19
0 58
1 4
4 1
7.7
9.7
<0 5*
0 5-1 0*
<1 0*
0 11*
0 21*
0.32*
0 43*
1 54*
RPS.%
_
-
0 0
14-34
2-65
10/14 2
43 8
56.4
63.3
10-50
3.7
48 4
96 6
109
90 4
96.3
-20-60
-30-70
-30-100
0.0
2.0
30 6
38.9
22.9
Imposex
VSD
_
-
0.0
2.2-4.3
2.9
3.7/3.7
3 9
4.0
4.1
_
3 2
4 4
5 1
5 0
5 0
5.0
-2 0-4.5
-4.5-6.0
-4.5-6.0
_
-
-
-
-
Comments Reference
No imposex Bryan et al . 1989
40-100% incidence
OX incidence Short et al . 1989
100% incidence,
reduced abundance
Bryan et al 1987
-
-
-
Some sterilization
Bryan et al . 1987
Normal females Gibbs et al. 1988
1/3 sterile, 160 capsules
All sterile, 2 capsules
All sterile, 0 capsules
All sterile, 0 capsules
All sterile
Limited sterility Gibbs et al . 1987
-50% sterile
All sterile
0% aborted egg Gibbs and Bryan 1986;
Gibbs et al . 1987
0% aborted egg capsules
15% aborted egg capsules
38% aborted egg capsules
79% aborted egg capsules
Concentrations changed from ug Sn/L or ug Sn/g to ug TBT/L or ug TBT/g dry weight.
-------
laboratory "control" snails exposed to 0.0036 ug/L and extent of penis and vas
deferens development increased significantly with increase in TBT exposure;
sterility occurred in some snails exposed to 0.26 ug/L. In a similar laboratory
experiment that began with snail egg capsules and lasted two years (Gibbs et al.
1988), imposex development was more severe. Field controls spawned and females
were normal in <0.0012 ug/L. In the laboratory, one-third of the snails exposed
to 0.0036 ug/L were sterile and 160 egg cases were produced. At >0.0093 ug/L
all females were sterile with only two undersized egg capsules produced.
Concentrations of TBT in females were 0.19 ug/g in the field, 0.58 ug/g in the
0.0036 ug/L treatment and from 1.39 to 7.71 ug/g in >0.0093 ug/L. Similar
concentrations of TBT (9.7 ug/g) were found in snails which became sterile after
they were placed in the Dart Estuary, UK where TBT concentrations range from
0.022 to 0.046 ug/L. Gibbs and Bryan (1986) and Gibbs et al. (1987) report
imposex and reproductive failures at other marine sites where TBT concentrations
in female snails range from 0.32 to 1.54 ug/g.
In summary, in both field and laboratory studies, concentrations of TBT
in water of about 0.001 ug/L or less and in tissues of about 0.2 ug/g or less
appear to not cause imposex in N. lapillus. Imposex begins to occur, and cause
some reproductive failure at about 0.004 ug/L with complete sterility occurring
after chronic exposure of sensitive early life-stages at >0.009 ug/L and for less
sensitive stages at 0.02 ug/L in some studies and greater than 0.2 ug/L in
others. If N. lapillus or similarly sensitive species are ecologically important
at specific sites, TBT concentrations < 0.001 ug/L may be required to limit
development of imposex.
Reproductive abnormalities have also been observed in the European flat
oyster (Thain 1986). After exposure for 75 days to a TBT concentration of 0.24
18
-------
ug/L, a retardation in the sex change from male to female was observed and larval
production was completely inhibited. A TBT concentration of 2.6 ug/L prevented
development of gonads.
Survival and growth of several commercially important saltwater bivalve
molluscs have been studied during acute and long-term exposures to TBT.
Mortality of larval blue mussels, Mytilus edulis. exposed to 0.0973 ug/L was 51%;
survivors were moribund and stunted (Beaumont and Budd 1984). Similarly, Dixon
and Prosser (1986) observed 79% mortality of mussel larva after 4 days exposure
to 0.1 ug/L. Growth of juvenile blue mussels was significantly reduced after
7 to 66 days at 0.31 to 0.3893 ug/L (Stromgren and Bongard 1987; Valkirs et al.
1985). Growth rates of mussels transplanted into San Diego Harbor were impacted
at sites where TBT concentrations exceeded 0.2 ug/L (Salazar and Salazar 1990b).
At locations where concentrations were less than 0.1 ug/L, the presence of
optimum environmental conditions for growth appear to limit or mask the effects
of TBT. Less than optimum conditions for growth may permit the effect of TBT
on growth to be expressed. Salazar et al. (1987) observed that 0.157 ug/L
reduced growth of mussels after 56 days exposure in the laboratory; a
concentration within less than a factor of two of that reducing growth in the
field. Similarly, Salazar and Salazar (1987) observed reduced growth of mussels
exposed to 0.070 ug/L for 196 days in the laboratory. The 66-day LC50 for 2.5
to 4.1 cm blue mussels was 0.97 ug/L (Valkirs et al. 1985,1987). Alzieu et al.
(1980) reported 30% mortality and abnormal shell thickening among Pacific oyster
larvae exposed to 0.2 ug/L for 113 days. Abnormal development was also observed
in exposures of embryos for 24 hrs or less to TBT concentrations > 0.8604 ug/L
(Robert and His 1981). Waldock and Thain (1983) observed reduced growth and
thickening of the upper shell valve of Pacific oyster spat exposed to 0.1460 ug/L
19
-------
for 56 days. Shell thickening in Crassostrea gigas was associated with tissue
concentrations of >0.2 mg/kg (Davies et al. 1988). Abnormal shell development
was observed in an exposure to 0.77 ug/L that began with embryos of the eastern
oyster, Crassostrea virginica. and lasted for 48 hours (Roberts, Manuscript).
Adult eastern oysters were also sensitive to TBT with reductions in condition
index after exposure for 57 days to > 0.1 ug/L (Henderson 1986; Valkirs et al.
1985). Salazar et al. (1987) found no effect on growth after 56 days exposure
to 0.157 ug/L of oysters C. virginica. Ostrea edulis and 0. lurida. Condition
of adult clams, Macoma nasuta. and scallops, Hinmites multirugosus were not
affected after 110 days exposure to 0.204 ug/L (Salazar et al. 1987).
Long-term exposures have been conducted with a number of saltwater
crustacean species. Johansen and Mohlenberg (1987) exposed adult Acartia tonsa
for five days to TBT and observed impaired egg production on days 3, 4 and 5 in
0.1 ug/L and only on day 5 in 0.01 and 0.05 ug/L. For the five days, overall
egg production was reduced markedly (25%) only in 0.1 ug/L. Davidson et al.
(1986a,1986b), Laughlin et al. (1983,1984b), and Salazar and Salazar (1985a)
reported that TBT acts slowly on crustaceans and that behavior might be affected
several days before mortality occurs. Survival of larval amphipods, Gammarus
oceanicus. was significantly reduced after eight weeks of exposure to TBT
concentrations > 0.2816 ug/L (Laughlin et al. 1984b). Hall et al. (1988b)
observed no effect of 0.579 ug/L on Gammarus sp. after 24 days. Developmental
rates and growth of larval mud crabs, Rhithropanopeus harrisii. were reduced by
a 15-day exposure to > 14.60 ug/L. R. harrisii might accumulate more TBT via
ingested food than directly from water (Evans and Laughlin 1984). TBTF, TBTO,
and TBTS were about equally toxic to amphipods and crabs (Laughlin et al.
1982,1983,1984a). Laughlin and French (1989) observed LC50 values for larval
20
-------
developmental stages of 13 ug/L for crabs (C. nauris) from California vs 33.6
ug/L for crabs from Florida. Limb malformations and reduced burrowing were
observed in fiddler crabs exposed to 0.5 ug/L (Weis and Kim 1988; Weis and
Perlmutter 1987). Arm regeneration was reduced in brittle stars exposed to 0.1
ug/L (Walsh et al. 1986a). Exposure to >0.1 ug/L during settlement of fouling
organisms reduced number of species and species diversity of communities
(Henderson 1986) . The hierarchy of sensitivities of phyla in this test was
similar to that of single species tests.
Exposure of embryos of the California grunion, Leuresthes tenuis. for ten
days to 74 ug/L caused a 50% reduction in hatching success (Newton et al. 1985).
At TBT concentrations between 0.14 and 1.72 ug/L, growth, hatching success, and
survival were significantly enhanced. In contrast, growth of inland silverside
larvae was reduced after 28 days exposure to 0.093 ug/L (Hall et al. 1988b) .
Juvenile Atlantic menhaden, Brevoortia tyrannus. avoided a TBT concentration of
5,437 ug/L and juvenile striped bass, Morone saxatilis. avoided 24.9 ug/L (Hall
et al. 1984). BCFs were 4,300 for liver, 1,300 for brain, and 200 for muscle
tissue of chinook salmon, Oncorhynchus tshawytscha. exposed to 1,490 ug/L for
96 hours (Short and Thrower 1986a,1986c).
TBT concentrations less than the Final Chronic Value of 0.0485 Mg/L from
Table 3 have been shown to affect the growth of early life-stages of commercially
important bivalve molluscs and survival of ecologically important copepods (Table
6; Text Table 2). Survival of the copepod Acartia tonsa was significantly
reduced in three tests in 0.029, 0.023 and 0.024 /Zg/L; 30, 27 and 51 percent of
control survival (Bushong et al. 1990). Survival decreased with increase in
exposure concentration but was not significantly affected in 0.012 /Ug/L.
Laughlin et al. (1987, 1988) observed a significant decrease in growth of
21
-------
Text Table 2. Summary of laboratory and field data on the effects of tributyltin on saltwater
organisms at concentrations less than the Final Chronic Value of 0.0485 Jlg/L
Species
Experimental Design3
Concentration (Ug/L)
Response
#2: F,M, 6-day duration,
>10 copepods/replicate,
4 replicates
control
0.007-0.012
0.023
0.048-0.102
71% survival
32% survival
19% survival13
0-14% survival
Reference
Copepod (nauplii-
adult) ,
Acartia tonsa
#1: F,M, 9 -day duration,
>10 copepods/replicate ,
4 replicates
Measured
control
0.029
0.05-0.5
77% survival
23% survival15
0-2% survival1*
Bushong et al .
1979
#3: F,M, 6-day duration,
>10 copepods/replicate,
4 replicates
control
0.006-0.010
0.024
0.051-0.115
59% survival
44-46% survival
30% survival15
2-35% survival15
Hard clam (4 hr
larvae -
metamorphosis),
Mercenaria
mercenaria
Pacific oyster (spat),
Crassostrea gigas
R,M, 14-day duration,
<150 larvae/replicate
three replicates. Measured =
80-100% nominal at t =
0-4 hr; 20-30% at t = 24 hr
R,N, 48-day duration,
20 spat/treatment
Nominal
control
0.01-0.5
Nominal
control
0.01-0.05
control
0.01-0.2
0.02-0.2
100% Growth
(Valve length)
-75%-22% Growth
(Valve length)b
shell thickening
100% Growth
(Valve length)
101% Growth (Value
length)
0-72% Growth
(Valve length)b
Laugh1in et al.
1987,1988
Lawler and
Aldric 1987
-------
Text Table 2 Cont.
Species
Experimental Design*
Concentration (ttg/L)
Response
Reference
Pacific oyster (spat)
Crassostrea gigas
R,N, 49-day duration,
0.7 to 0.9 g/spat
Nominal
control
0.002
0.02-2.0
no shell thick-
ening
shell thickening
proportional to
concentration
increase
Thain, et al.
1987
to
U)
Pacific oyster
(larvae and spat),
Crassostrea gigas
Field
R.M/N, 21-day duration,
75,000 larvae/replicate
Measured
0.011-0.015
-0.018-0.060
Measured
0.24,0.29,
0.69
Nominal
control, 0.1,
0.05,0.025
no shell thick-
ening
shell thickening
and decreased
meat weight
mortality 100%
by day 1
mortality 100%
in 0.05 and 1.0
86% in 0.025 /ig/L
* R = renewal; F - flow-through, N = nominal, M = measured.
b Significantly different from controls.
Springborn
Bionomics ,
Inc. 1984a
European oyster
(spat),
Ostrea edulis
R,N
50
, 20 -day duration,
spat/treatment
control
0.02-2.0
control
0.02-2.0
100% length
76-81% lengthb
202% weight gain
151-50% weight
gain
Thain and
Waldock 1985
-------
hard clam (Mercenaria mercinaria) larvae exposed for 14 days to >0.01 /Xg/L (Text
Table 2). Growth rate (increase in valve length) was 75% of controls in 0.01
/ig/L, 63% in 0.025 /Jg/L, 59% in 0.05 /ig/L, 45% in 0.1 Mg/L, 29% in 0.25 /Ug/L and
2.2% in 0.5 /ig/L. A five-day exposure followed by nine days in TBT-free water
produced similar responses and little evidence of recovery.
Pacific oyster fCrassostrea gigas) spat exhibited shell thickening in 0.01
and 0.05 /ig/L and reduced valve lengths in >0.02 Mg/L (Lawler and Aldrich 1987;
Text Table 2). Increase in valve length was 101% of control lengths in 0.01
Mg/L, 72% in 0.02 jZg/L, 17% in 0.05 Mg/L, 35% in 0.1 Mg/L and 0% in 0.2 JZg/L.
Shell thickening was also observed in this species exposed to >0.02 /ig/L for 49
days (Thain et al. 1987). They predicted from these data that approximately
0.008 Mg/L would be the maximum TBT concentration permitting culture of
commercially acceptable adults. Their field studies agreed with laboratory
results showing "acceptable" shell thickness where TBT concentrations averaged
0.011 and 0.015 Mg/L but not at higher concentrations. Decreased weights of
oyster meats were associated with locations where there was shell thickening.
Survival of Crassostrea gigas larvae exposed for 21 days was reduced in 0.025
/ig/L (Springborn Bionomics 1984a) . No larvae survived in >0.050 /ig/L.
Growth of spat of the European oyster (Ostrea edulis) was reduced at >0.02
/ig/L (Thain and Waldock 1985; Text Table 2). Spat exposed to TBT in static tests
were 82% of control lengths and 75% of control weights; extent of impact
increased with increased exposure. In these static and flow-through tests at
exposures at about 0.02 Mg/Li weight gain was identical; i.e., 35% of controls.
Growth of larger spat was marginally reduced by 0.2392 Mg/L (Thain 1986; Thain
and Waldock 1985).
The National Guidelines (Stephan et al. 1985; pp 18 and 54) requires that
24
-------
the criterion be lowered if sound scientific evidence indicates that adverse
effects might be expected on important species. The above data demonstrate that
reductions in growth occur in commercially or ecologically important saltwater
species at concentrations of TBT less than the Final Chronic Value of 0.0485
/ig/L derived using Final Acute Values and Acute-Chronic Ratios from Table 3.
Therefore, EPA believes the Final Chronic Value should be lowered to 0.01 jUg/L
to limit unacceptable impacts on Acartia tonsa. Mercenaria mercenaria.
Crassostrea gigas and Ostrea edulis observed at 0.02 /Xg/L. At this criteria
concentration, imposex would be expected in Ilyanassa obsoleta. Nucella lapillus
and similarly sensitive neogastropods; populations of N. lapillus and similarly
sensitive snails with direct development might be impacted and growth of
Mercenaria mercenaria might be somewhat lowered.
Unused Data
Some data concerning the effects of TBT on aquatic organisms were not used
because the tests were conducted with species that are not resident in North
America (e.g., Allen et al. 1980; Carney and Paulini 1964; Danil'chenko 1982;
Deschiens and Floch 1968; Deschiens et al. 1964,1966a,1966b; de Sousa and Paulini
1970; Frick and DeJimenez 1964; Hopf and Muller 1962; Kubo et al. 1984; Nishuichi
and Yoshida 1972; Ritchie et al. 1964; Seiffer and Schoof 1967; Shiff et al.
1975; Smith et al. 1979; Tsuda et al. 1986; Upatham 1975; Upatham et al.
1980a,1980b; Webbe and Sturrock 1964).
Alzieu (1986), Cardarelli and Evans (1980), Cardwell and Sheldon (1986),
Cardwell and Vogue (1986), Champ (1986), Chau (1986), Eisler (1989), Envirosphere
Company (1986), Gibbs and Bryan (1987), Good et al. (1980), Guard et al. (1982),
Hall (1988), Hall and Pinkney (1985), Hodge et al. (1979), International Joint
25
-------
Commission (1976), Jensen (1977), Kimbrough (1976), Kumpulainen and Koivistoinen
(1977), Laughlin (1986), Laughlin and Linden (1985), Laughlin et al. (1984a),
McCullough et al. (1980), Monaghan et al. (1980), North Carolina Department of
Natural Resources and Community Development (1983,1985), Rexrode (1987), Seligman
et al. (1986), Slesinger and Dressier (1978), Stebbing (1985), Thayer (1984),
Thompson et al. (1985), U.S. EPA (1975,1985b), U.S. Navy (1984), Valkirs et al.
(1985), von Rumker et al. (1974), Walsh (1986) and Zuckerman et al. (1978)
compiled data from other sources. Studies by Gibbs et al. (1987) were not used
because data were from the first year of a two-year experiment reported in Gibbs
et al. (1988).
Results were not used when the test procedures, test material, or results
were not adequately described (e.g., Bruno and Ellis 1988; Cardwell and Stuart
1988; Chau et al. 1983; Danil'chenko and Buzinova 1982; de la Court 1980;
Deschiens 1968; EG&G Bionomics 1981b; Filenko and Isakova 1980; Holwerda and
Herwig 1986; Kelly et al. 1990; Kolosova et al. 1980; Laughlin 1983; Lee 1985;
Nosov and Kolosova 1979; Smith 1981c; Stroganov et al. 1972,1977). The 96-hr
LC50 of 0.01466 Mg/L reported by Becerra-Huencho (1984) for post larvae of the
hard clam, Mercenaria mercenaria. was not used because results of other studies
with embryos, larvae, and post larvae of the hard clam where acutely lethal
concentrations range from 0.6 to 4.0 /ig/L (Tables 1 and 6) cast doubt on this
LC50 value. Data from the life-cycle test with sheepshead minnows (Ward et al.
1981) were not used because ratios of measured and nominal concentrations were
inconsistent within and between tests suggesting problems in delivering TBT,
analytical chemistry or both. Results of some laboratory tests were not used
because the tests were conducted in distilled or deionized water without addition
of appropriate salts (e.g., Gras and Rioux 1965; Kumar Das et al. 1984). The
26
-------
concentration of dissolved oxygen was too low in tests reported by EG&G Bionomics
(1981a). Douglas et al. (1986) did not observe sufficient mortalities to
calculate a useful LC50.
Data were not used when TBT was a component of a formulation, mixture,
paint, or sediment (Boike and Rathburn 1973; Cardarelli 1978; Deschiens and Floch
1970; Goss et al. 1979; Laughlin et al. 1982; Maguire and Tkacz 1985; Mattiessen
and Thain 1989; North Carolina Department of Natural Resources and Community
Development 1983; Pope 1981; Quick and Cardarelli 1977; Salazar and Salazar
1985a,1985b; Santos et al. 1977; Sherman 1983; Sherman and Hoang 1981; Sherman
and Jackson 1981; Walker 1977; Weisfeld 1970), unless data were available to show
that the toxicity was the same as for TBT alone.
Data were not used when the test organisms were infested with tapeworms
(e.g., Hnath 1970). Mottley (1978) and Mottley and Griffiths (1977) conducted
tests with a mutant form of an alga. Results of tests in which enzymes, excised
or homogenized tissue, or cell cultures were exposed to the test material were
not used (e.g., Blair et al. 1982; Josephson et al. 1989). Tests conducted with
too few test organisms were not used (e.g., EG&G Bionomics 1976; Good et al.
1979). High control mortalities occurred in tests reported by Salazar and
Salazar (Manuscript) and Valkirs et al. (1985). Some data were not used because
of problems with the concentration of the test material (e.g., Springborn
Bionomics 1984b; Stephenson et al. 1986; Ward et al. 1981). BCFs were not used
when the concentration of TBT in the test solution was not measured (Laughlin
et al. 1986b; Paul and Davies 1986) or were highly variable (Laughlin and French
1988). Reports of the concentrations in wild aquatic animals were not used if
concentrations in water were unavailable or excessively variable (Davies et al.
1987; Davies and McKie 1987; Hall 1988; Han and Weber 1988; Wade et al. 1988.
27
-------
Summary
The acute toxicity values for thirteen freshwater animal species range from
1.14 ug/L for a hydra (Hydra oligactis) to 24,600 ug/L for a clam (Elliptic
complanatus) . There was no apparent trend in sensitivities with taxonomy; fish
were nearly as sensitive as the most sensitive invertebrates and more sensitive
than others. When the much less sensitive clam was not considered, the remaining
species sensitivities varied by a maximum of 8.7 times. Three chronic toxicity
tests have been conducted with freshwater animals. Reproduction of Daphnia
magna was reduced by 0.2 ug/L, but not by 0.1 ug/L, and the Acute-Chronic Ratio
is 30.41. In another test with D. magna reproduction and survival was reduced
at 0.34 ug/L but not at 0.19, and the Acute-Chronic Ratio is 44.06. Weight of
fathead minnows was reduced by 0.45 ug/L, but not by 0.15 ug/L, and the acute-
chronic ratio for this species was 10.01. Bioconcentration of TBT was measured
in rainbow trout, Oncorhvnchus mykiss. at 406 times the water concentration for
the whole body. Growth of thirteen species of freshwater algae was inhibited
by concentrations ranging from 56.1 to 1,782 ug/L.
Acute values for 27 species of saltwater animals range from 0.61 ug/L for
the mysid, Acanthomysis sculpta. to 204.4 ug/L for adult European flat oysters,
Ostrea edulis. Acute values for the twelve most sensitive genera, including
molluscs, crustaceans, and fishes, differ by less than a factor of 4. Larvae
and juveniles appear to be more sensitive than adults. A life-cycle toxicity
test has been conducted with the saltwater mysid, Acanthomysis sculpta. The
chronic value for A. sculpta was 0.1308 ug/L based on reduced reproduction and
the acute-chronic ratio was 4.664. Bioconcentration factors for three species
of bivalve molluscs range from 192.3 for soft parts of the European flat oyster
to 11,400 for soft parts of the Pacific oyster, Crassostrea gigas. Tributyltin
28
-------
chronically affects certain saltwater copepods, gastropods, and pelecypods at
concentrations less than those predicted from "standard" acute and chronic
toxicity tests. Survival of the copepod Acartia tonsa was reduced in >0.023
Mg/L- Growth of larvae or spat of two species of oysters, Crassostrea gigas and
Ostrea edulis was reduced in about 0.02 Mg/L; some C. gigas larvae died in 0.025
Alg/L. Generally concentrations <0.01 /ig/L have not been demonstrated to affect
sensitive life-stages of saltwater organisms. These data demonstrate that
reductions in growth occur in commercially or ecologically important saltwater
species at concentrations of TBT less than the Final Chronic Value of 0.0485 /ig/L
derived using Final Acute Values and Acute-Chronic Ratios from Table 3.
Therefore, EPA believes the Final Chronic Value should be lowered to 0.01 /Llg/L
to limit unacceptable impacts on Acartia tonsa. Mercenaria mercenaria.
Crassostrea gigas and Ostrea edulis observed at 0.02 Mg/L- At this criteria
concentration, imposex would be expected in Ilyanassa obsoleta. Nucella lapillus
and similarly sensitive neogastropods; populations of N. lapillus and similarly
sensitive snails with direct development might be impacted and growth of
Mercenaria mercenaria might be somewhat lowered.
National Criteria
The procedures described in the "Guidelines for Deriving Numerical National
Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
indicate that, except possibly where a locally important species is very
sensitive, freshwater aquatic organisms and their uses should not be affected
unacceptably if the four-day average concentration of tributyltin does not exceed
0.063 Mg/L more than once every three years on the average and if the one-hour
average concentration does not exceed 0.46 /ig/L more than once every three years
29
-------
on Che average.
The procedures described in the "Guidelines for Deriving Numerical National
Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
indicate that, except possibly where a locally important species is very
sensitive, saltwater aquatic organisms and their uses should not be affected
unacceptably if the four-day average concentration of tributyltin does not exceed
0.010 /ig/L more than once every three years on the average and if the one-hour
average concentration does not exceed 0.36 Mg/L more than once every three years
on the average.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983a)
and the Foreword of this document, a water quality criterion for aquatic life
has regulatory impact only if it has been adopted in a state water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the U.S.
EPA, states designate one or more uses for each body of water or segment thereof
and adopt criteria that are consistent with the use(s) (U.S. EPA 1983b,1987).
In each standard a state may adopt the national criterion, if one exists, or,
if adequately justified, a site-specific criterion. (If the site is an entire
state, the site-specific criterion is also a state-specific criterion.)
Site-specific criteria may include not only site-specific criterion
concentrations (U.S. EPA 1983b), but also site-specific, and possibly
pollutant-specific, durations of averaging periods and frequencies of allowed
excursions (U.S. EPA 1985c). The averaging periods of "one hour" and "four
days" were selected by the U.S. EPA on the basis of data concerning the speed
30
-------
with which some aquatic species can react to increases in the concentrations of
some aquatic pollutants, and "three years" is the Agency's best scientific
judgment of the average amount of time aquatic ecosystems should be provided
between excursions (Stephan et al. 1985; U.S. EPA 1985c). However, various
species and ecosystems react and recover at greatly differing rates. Therefore,
if adequate justification is provided, site-specific and/or pollutant-specific
concentrations, durations, and frequencies may be higher or lower than those
given in national water quality criteria for aquatic life.
Use of criteria, which have been adopted in state water quality standards,
for developing water quality-based permit limits and for designing waste
treatment facilities requires selection of an appropriate wasteload allocation
model. Although dynamic models are preferred for the application of these
criteria (U.S. EPA 1985c), limited data or other considerations might require
the use of a steady-state model (U.S. EPA 1986).
Guidance on mixing zones and the design of monitoring programs is also
available (U.S. EPA 1985b).
31
-------
Table 1. Acute Toxicity of Tributyltin to Aquatic Animals
Species
Hydra,
Hydra littoralis
Hydra.
Hydra littoralis
Hydra.
Hydra oligactis
Hydra.
Chlorohydra viridissmia
Annelid (9 mg),
Lumbriculus variegatus
OJ
10 Freshwater clam,
(113 ran TL; 153 g)
Elliptic complanatus
Cladoceran,
Daphnia magna
Cladoceran (adult),
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Cladoceran (<24 hr),
Daphnia magna
Amphipod,
Gammarus pseudol imnaeus
Method* Chemical"
S,H TBTO
(97.5%)
S,H TBTO
(97.5%)
S.H TBTO
(97.5%)
S,M TBTO
(97.5%)
F,H TBTO
(96%)
S,U TBTO
(95%)
S,U TBTO
S,U TBTC
S,U TBTO
(95%)
R,M TBTO
97.5%
F.H TBTO
(96%)
F.M TBTO
(96%)
Hardness LC50
(mg/L as or EC50
CaCO,) (ug/L)c
FRESHWATER SPECIES
100 1.11
120 1.30
100 1.14
120 1.80
51.8 5.4
24,600
66.3
5.26
1.58
172 11.2
51.5 4.3
51.8 3.7
Species Hean
Acute Value
(uq/L) References
TAI Environmental Sciences,
Inc. 1989a
1.201 TAI Environmental Sciences,
Inc. 1989b
1.14 TAI Environmental Sciences,
Inc. 1989a
1.80 TAI Environmental Sciences,
Inc. 1989b
5.4 Brooke et al. 1986
24,600 Buccafusco 1976a
Foster 1981
Meador 1986
LeBlanc 1976
ABC Laboratories, Inc. 1990c
4.3 Brooke et al. 1986
3.7 Brooke et al. 1986
-------
Table 1. (Continued)
Species Method"
Mosquito (larva), S,M
Culex sp.
Rainbow trout S,U
(45 nm TL; 0.68 g)
Oncorhynchus mykiss
Rainbow trout (juvenile), F,H
Oncorhynchus mvkiss
Rainbow trout (1.47 g), F,H
Oncorhvnchus mvkiss
Rainbow trout (1.4 g), F.M
Oncorhynchus mvkiss
w Lake trout (5.94 g), F.M
w Salvelinus naymaycush
Fathead minnow (juvenile), F.M
Pimephales promelas
Channel catfish S,U
(54 nm Th; 1.9 g)
Ictalurus punctatus
Channel catfish F,M
(juvenile),
Ictalurus punctatus
Bluegill. S,U
Lepomis macrochirus
Bluegill S,U
(0.67g; 36 mm TL),
Lepomis macrochirus
Bluegill (1.01 g), F.M
Lepomis macrochirus
Hardness
(mg/L as
Chemical" CaCO,)
TBTO 51.5
(96%)
TBTO
(95%)
TBTO 50.6
(96%)
TBTO 135
(97%)
TBTO 44
(97.5%)
TBTO 135
(97%)
TBTO 51.5
(96%)
TBTO
(95%)
TBTO 51.8
(96%)
TBTO
TBTO
(95%)
TBTO 44
97.5%
LC50
or EC50
(ug/L)1
10.2
6.5
3.9
3.45
7.1
12.73
2.6
11.4
5.5
227.4
7.2
8.3
Species Mean
Acute Value
(ug/L) References
10.2 Brooke et al. 1986
Buccafusco et al. 1978
Brooke et al. 1986
Martin et al. 1989
4.571 ABC Laboratories, Inc. 1990s
12.73 Martin et al. 1989
2.6 Brooke et al. 1986
Buccafusco 1976a
5.5 Brooke et al. 1986
Foster 1981
Buccafusco 1976b
8.3 ABC Laboratories. Inc. 1990b
-------
Table 1. (Continued)
Species
Lug worm (larva),
Arenicola cristate
Lugworm ( larva),
Arenicola cristata
Polychaete (juvenile),
Neanthes arenaceodentata
Polychaete (adult),
Neanthes arenaceodentata
Blue mussel (larva),
Mvtilus edulis
*• Blue mussel (adult).
Myti I us edulis
Blue mussel (adult),
Mytilus edulis
Pacific oyster (larva),
Crassostrea gigas
Pacific oyster (adult),
Crassostrea gigas
Eastern oyster (embryo),
Crassostrea virginica
Eastern oyster (embryo),
Crassostrea virginica
Eastern oyster (embryo),
Crassostrea virginica
Eastern oyster
Method* Chemical"
S.U TBTO
S.U TBTA
S.U TBTO
S.U TBTO
R,- TBTO
R,- TBTO
S.U TBTO
R.- TBTO
R,- TBTO
S.U TBTO
R.U TBTC
R.U TBTC
R.U TBTC
LC50
Salinity or EC50
(g/kg) (ug/L)°
SALTWATER SPECIES
28 -2-4
28 -5-10
33-34 6.812
33-34 21.41*
2.238
36.98'
33-34 34.06'
1.557
282.2*
22 0.8759
18-22 1.30
18-22 0.71
18-22 3.96°
Species Mean
Acute Value
(ug/L)
-
-5.03
-
6.812
-
-
2.238
-
1.557
-
-
-
0.9316
Crassostrea virginica
References
Walsh et al. 1986b
Walsh et al. 1986b
Salazar and Salazar,
Manuscript
Salazar and Salazar,
Manuscript
Thain 1983
Thain 1983
Salazar and Salazar,
Manuscript
Thain 1983
Thain 1983
EG&G Bionomics 1977
Roberts, Manuscript
Roberts, Manuscript
Roberts, Manuscript
-------
Table 1. (Continued)
Species
European flat oyster
(adult),
Ostrea edul is
Hard clam
(post larva),
Hercenaria mercenaria
Hard clam (embryo),
Hercenaria mercenaria
Hard clam (larva),
Hercenaria mercenaria
Copepod ( juveni le) ,
Eurytemora af finis
u Copepod (subadult),
01 Eurytemora af finis
Copepod (subadult),
Eurytemora af finis
Copepod (adult),
Acartia tonsa
Copepod (subadult),
Acartia tonsa
Copepod (adult),
Nitocra spinipes
Copepod (adult),
Nitocra spinipes
Mysid (juvenile),
Acanthomysis sculpta
Mysid (adult),
Method*
R.-
S.U
R.U
R.U
F,M
F.M
F,M
R.U
F.M
s.u
s.u
R,M
F.M
Salinity
Chemical" (g/kg)
TBTO
TBTC
TBTC 18-22
TBTC 18-22
TBTC 10.6
TBT 10
TBT 10
TBTO
(95%)
TBT • 10
TBTF 7
TBTO 7
f
f
LC50
or EC50
(ug/L)'
204.4
0.0146611
1.13
1.65
2.2
2.5
1.4
0.6326
1.1
1.877
1.946
0.42
1.68"
Species Mean
Acute Value
(ug/L) References
204.4 Thain 1983
Becerra-Huencho 1984
Roberts. Manuscript
1.365 Roberts, Manuscript
Hall et al. 1988a
Bushong et al. 1987; 1988
1.975 Bushong et al. 1987; 1988
U'ren 1983
1.1 Bushong et al. 1987; 1988
Linden et al. 1979
1.911 Linden et al. 1979
Davidson et al. 1986a,19l
Valkirs et al. 1985
Acanthomysis sculpta
-------
Table 1. (Continued)
Species
Mysid (juvenile),
Acanthomysis sculpta
Mysid (juvenile),
Metamysidopsis elongata
Mysid (subadult),
Hetamysidopsis elongata
Hysid (adult),
Hetamysidopsis elongata
Hysid (adult),
Hetamysidopsis elongata
Hysid (<1 day).
Hysidopsis bahia
Mysid (5 day).
Mysidopsis bahia
Mysid (10 day),
Hysidopsis bahia
Amphipod (subadult),
Gammarus sp.
Amphipod (adult),
Gammarus sp.
Amphipod (adult),
Orchestia traskiana
Grass shrimp (adult),
Palaemonetes pugio
Grass shrimp (subadult),
Palaemonetes sp.
American lobster (larva),
Homarus americanus
Method"
F,H
S.U
S.U
S.U
S,U
F.M
F.M
F.M
F.M
F.M
R,M
F.U
F.M
R,U
Chemical"
f
TBTO
TBTO
TBTO
TBTO
TBTC
TBTC
TBTC
TBT
TBT
TBTO
TBTO
TBT
TBTO
Salinity
(g/kg)
33-34
33-34
33-34
33-34
19-22
19-22
19-22
10
10
30
-
10
32
LC50
or EC50
(ug/L)'
0.61
<0.9732
1.946'
2.433"
6.812*
1.1
2.0
2.2
1.3
5.3"
>14.60g
20
>31
1.745"
Species Nean
Acute Value
(ug/L) References
0.61 Valkirs et al. 1985
Salazar and Salazar,
Manuscript
Salazar and Salazar,
Manuscript
Salazar and Salazar,
Manuscript
<0.9732 Salazar and Salazar,
Manuscript
Goodman et al. 1988
Goodman et al. 1988
1.692 Goodman et al. 1988
Bushong et al. 1988
1.3 Bushong et al. 1988
>14.60 Laugh 1 in et al. 1982
Clark et al. 1987
>31 Bushong et al. 1988
1.745 Laughlin and French
-------
Table 1. (Continued)
Salinity
Species Method* Chemical' (g/kg)
Shore crab (larva), R,- TBTO
Carcinus maenas
Mud crab (larva), R.U TBTS 15
Rhithropanopeus harrisii
Mud crab (larva), R,U TBTO 15
Rhithropanopeus harrisii
Shore crab (larva), R.U TBTO 32
Hemigrapsus nudus
Amphioxus, F.U TBTO
Branchi os toma caribaeum
Atlantic menhaden F.M TBT 10
(juvenile),
Brevoortia tyrannus
Atlantic menhaden F.M TBT 10
(juvenile),
Brevoortia tyrannus
Sheepshead minnow S.U TBTO 20
(juvenile),
Cypr i nodon variegatus
Sheepshead minnow S,U TBTO 20
(juvenile),
Cypr i nodon variegatus
Sheepshead minnow S,U TBTO 20
(juvenile),
Cypr i nodon variegatus
Sheepshead minnow F.M TBTO 28-32
(33-49 nm),
Cypr i nodon variegatus
LC50
or EC50
(ua/L)'
9.732
>24.3g
34.90°
83.28°
,10
4.7
5.2
16.54
16.54
12.65
2.315°
Species Mean
Acute Value
(ug/L) References
9.732 Thain 1983
Laughlin et al. 1983
34.90 Laughlin et al. 1983
83.28 Laughlin and French
<10 Clark et al. 1987
Bushong et al. 1987;
4.944 Bushong et al. 1987;
EG&G Bionomics 1979
EG&G Bionomics 1979
EG&G Bionomics 1979
1980
1988
1988
EG&G Bionomics 1981d
Sheepshead minnow
(juvenile).
Cypr i nodon variegatus
F,M
TBTO
15
12.31
Walker 1989a
-------
Table 1. (Continued)
00
Species Method*
Sheepshead minnow F,M
(subadult),
Cyprinodon variegatus
Mummichog (adult), S,U
Fundulus heteroclitus
Mummichog (juvenile), F.M
Fundulus heteroc I i tus
Mummichog (larval), F.M
Fundulus heteroclitus
Mummichog (subadult), F,M
Fundulus heteroclitus
Chinook salmon (juvenile), S,M
Oncorhynchus tshawytscha
Inland silverside (larva), F.M
Henidia beryllina
Atlantic silverside F.M
Menidia menial ia
Salinity
Chemical" (g/kq)
TBT 10
TBTO 25
(95%)
TBTO 2
TBT 10
TBT 10
TBTO 28
TBT 10
TBT 10
LC50 Species Mean
or EC50 Acute Value
(ug/L)c (ug/L) References
25.9 9.037 Bushong et al. 1988
23.36 - EG&G Bionomics 1976
17.2 - Pinkney et al. 1989
23.4 - Bushong et al. 1988
23.8 21.24 Bushong et al. 1988
1.460 1.460 Short and Thrower 1986b;1987
3.0 3.0 Bushong et al. 1987; 1988
8.9 8.9 Bushong et al. 1987; 1988
' S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
° TBTC = tributyltin chloride; TBTF = tributyltin fluoride; TBTO = tributyltin oxide; TBTS = tributyltin sulfide. Percent purity is given in parentheses
when available.
c Concentration of the tributyltin cation, not the chemical. If the concentrations were not measured and the published results were not reported to be
adjusted for purity, the published results were multiplied by the purity if it was reported to be less than 95%.
" Value not used in determination of Species Mean Acute Value (see text).
* Value not used in determination of Species Mean Acute Value because data are available for a more sensitive life stage.
' The test organisms were exposed to leachate from panels coated with antifouling paint containing a tributyltin polymer and cuprous oxide. Concentrations
of TBT were measured and the authors provided data to demonstrate the similar toxicity of a pure TBT compound and the TBT from the paint formulation.
* LC50 or EC50 calculated or interpolated graphically based on the authors' data.
-------
Table 2. Chronic Toxicity of Tributyltin to Aquatic Animals
Species
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Fathead minnow,
Piraephales promelas
Copepod,
Eurytemora af finis
Copepod,
Eurytemora aff inis
Mysid.
Acanthomysis sculpt a
Test3 Chemical6
LC TBTO
(96%)
LC TBTO
(100%)
ELS TBTO
(96%)
LC TBTC
LC TBTC
LC d
(mg/L as
CaCOO
j
FRESHWATER
51.5
160-174
51.5
SALTWATER
10.3e
14.6e
-
Limits Chronic Value
(ug/L)c (uq/L) Reference
SPECIES
0.1-0.2 0.1414 Brooke et al. 1986
0.19-0.34 0.2542 ABC Laboratories, Inc. 1990d
0.15-0.45 0.2598 Brooke et al. 1986
SPECIES
<0.088 <0.088 Hall et al. 1987;1988a
0.100-0.224 0.150 Hall et al. 1987;1988a
0.09-0.19 0.1308 Davidson et al. 1986a.1986b
LC = life-cycle or partial life-cycle; ELS = early life-stage.
b TBTO = tributyltin oxide; TBTC = tributyltin chloride. Percent purity is given in parentheses when available.
c Measured concentrations of the tributyltin cation.
The test organisms were exposed to leachate from panels coated with antifouling paint containing a tributyltin polymer and cuprous oxide. Concentrations
of TBT were measured and the authors provided data to demonstrate the similar toxicity of a pure TBT compound and the TBT from the paint formulation.
e Salinity (g/kg).
-------
Table 2. (Continued)
Acute-Chronic Ratios
Species
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Fathead minnow.
Pimephales promelas
Cope pod.
Eurvtemora aff inis
Cope pod.
Eurytemora aff inis
Mysid,
Acanthomysis sculpta
Hardness
(mg/L as Acute Value
CaCtL) (uq/L)
51.5 4.3
160-174 11.2
51.5 2.6
1.975
1.975
0.61a
Chronic Value
(uq/L)
0.1414
0.2542
0.2598
<0.088
0.150
0.1308
Ratio
30.41
44.06
10.01
>22.44
13.17
4.664
a Reported by Valkirs et al. (1985).
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Rank*
12
11
10
9
6
5
4
3
2
Genus Mean
Acute Value
(ug/L)
24,600
12.73
10.2
8.3
5.5
5.4
4.571
4.3
3.7
2.6
1.80
1.170
les
FRESHWATER SPECIES
Freshwater clam,
Elliptic campIanatus
Lake trout,
Salvelinus navmaycush
Mosquito,
Culex sp.
Bluegi LI,
Lepomis macrochirus
Channel catfish,
Ictalurus punctatus
Annelid,
Lumbriculus variegatus
Rainbow trout,
Oncorhyncus mykiss
Cladoceran,
Daphnia magna
Amphipod,
Gammarus pseudolimnaeus
Fathead minnow,
Pimephales promelas
Hydra
Chlorohydra viridissmia
Hydra,
Hydra littoralis
Hydra,
Hydra oligactis
Species Mean
Acute Value
Cug/D"
24.600
12.73
10.2
8.3
5.5
5.4
4.571
4.3
3.7
2.6
1.80
1.201
1.14
Species Mean
Acute-Chronic
Ratio'
36.60
10.01
-------
Table 3. (continued)
lank*
25
24
23
22
21
20
19
18
17
16
15
Genus Mean
Acute Value
(ug/L)
204.4
83.28
34.90
24.90
21.24
>14.60
<10
9.732
6.812
9.037
5.167
Species Mean Species Nean
Acute Value Acute-Chronic
Species (ug/L)B Ratio*
SALTWATER SPECIES
European flat oyster, 204.4
Ostrea edul i s
Shore crab, 83.28
Hemigrapsus nudus
Hud crab, 34.90
Rh i thropanopeus Harris! i
Grass shrimp, 20
Palaemonetes pugio
Grass shrimp, >31
Palaemonetes sp.
Hummichog, 21.24
Fundulus heteroe 1 i tus
Amphipod, >14.60
Orchestia traskiana
Amphioxus <10
Branch i os toma caribaeum
Shore crab, 9.732
Carcinus maenas
Polychaete, 6.812
Neanthes arenaceodentata
Sheepshead minnow, 9.037
Cyprinodon variegatus
Inland silverside, 3.0
Henidia beryl Una
Atlantic silverside,
Henidia menidia
8.9
-------
Table 3. (continued)
Ul
Rank*
14
13
12
11
10
9
8
7
6
5
4
3
Genus Mean
Acute Value
Cug/L)
-5.0
4.944
2.238
1.975
1.911
1.745
1.692
1.460
1.365
1.3
1.204
1.1
Species
Lugworm,
Arenicola cristata
Atlantic manhaden,
Brevoortia tyrannus
Blue mussel,
Hytilus edulis
Copepod,
Eurytemora af finis
Copepod,
Nit ocr a spinipes
American lobster,
Homarus americanus
Mysid,
Mysidopsis bah i a
Chinook salmon,
Oncorhvnchus tshawytscha
Hard clam,
Hercenaria mercenaria
Amphipod,
Gammarus sp.
Pacific oyster,
Crassostrea qigas
Eastern oyster,
Crassostrea virgim'ca
Copepod,
Acartia tonsa
Species Mean
Acute Value
(ug/L>"
-5.0
4.944
2.238
1.975
1.911
1.745
1.692
1.460
1.365
1.3
1.557
0.9316
1.1
Species Mean
Acute-Chronic
Ratio'
-
-
-
27.24'
-
-
-
-
-
-
-
-
-
-------
Table 3. (continued)
Genus Mean Species Mean Species Mean
Acute Value Acute Value Acute-Chronic
Rank* (ug/L) Species Cua/u" Ratio'
<0.9732 Mysid, <0.9732"
Hetacnvsidopsis elongata
0.61 Mysid, 0.61 4.664
Acanthomysis sculpta
' Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
" From Table 1.
c From Table 2.
" This was used as a quantitative value, not as a "less than" value in the calculation of the Final Acute Value.
This was the lowest concentration used in the toxicity test and it killed 63% of the exposed my s ids.
" See text for justification of this value.
-------
Table 3. (continued)
Fresh Water
Final Acute Value = 0.9177 ug/L
Criterion Maximum Concentration = (0.9177 ug/L) / 2 = 0.4589 ug/L
Final Acute-Chronic Ratio = 14.69 (see text)
Final Chronic Value = (0.9177 ug/L) / 14.69 = 0.0625 ug/L
Salt Water
Final Acute Value = 0.7128 ug/L
Criterion Maximum Concentration = (0.7128 ug/L) / 2 = 0.3564 ug/L
Final Acute-Chronic Ratio = 14.69 (see text)
Final Chronic Value = (0.7128 ug/L) / 14.69 = 0.0485 ug/L
Final Chronic Value = 0.010 ug/L (lowered to protect growth of commercially important molluscs and survival of the
ecologically important copepod Acartia tonsa: see text)
-------
Table 4. Toxicity of Tributyltin to Aquatic Plants
Hardness
(mg/L as
Species Chemical3 CaCO^)
Alga, TBTC
Bumi 1 leriopsis
f i I iformis
Alga, TBTC
Klebsormidium marinum
Alga, TBTC
Monodus subterraneus
Alga, TBTC
Raphidonema longiseta
Alga, TBTC
Tribonema a equate
*»
O> Blue-green alga, TBTC
Osci 1 latoria sp.
Blue-green alga, TBTC
Synechococcus
leopoliensis
Green alga, TBTC
Chlarnvdomonas dysosmas
Green alga, TBTC
ChloreUa emersonii
Green alga. TBTC
Kirchneriella contorta
Green alga, TBTC
Monoraphidium pusil I urn
Green alga, TBTC
Scenedesmus
obtusiusculus
Duration Concentration
^days) Effect (ug/L>b
Reference
FRESHWATER SPECIES
14
14
14
14
14
14
14
14
14
14
14
14
No
Ho
Ho
Ho
Ho
Ho
Ho
No
Ho
No
Ho
Ho
growth 111.4
growth 222.8
growth 1,782.2
growth 56.1
growth 111.4
growth 222.8
growth 111.4
growth 111.4
growth 445.5
growth 111.4
growth 111.4
growth 445.5
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
Blanck
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1986;
et al.
1984
1984
1984
1984
1984
1984
1984
1984
1984
1984
1984
1984
-------
Table 4. (continued)
Species
Green alga,
Selenastrum
capricornutum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Salinity
Chemical8 (g/kg)
TBTC
TBTO
TBTO 30
(BioMet Red)
TBTO 30
Duration
(days)
14
5
14
14
Effect
No growth
SALTWATER SPECIES
Algistatic
algicidal
EC50
(dry cell
weight)
EC50
(dry cell
weight)
Concentration
Cug/L)b
111.4
0.9732-17.52
>17.52
>0.1216; <0.2433
0.06228
Reference
Blanck 1986;
Blanck et al. 1984
Thain 1983
EG&G Bionomics 1981 c
EG&G Bionomics 1981c
TBTC = tributylttn chloride; TBTO = tributyltin oxide. Percent purity is given in parenthese when available.
Concentration of the tributyltin cation, not the chemical. If the concentrations were not measured and the published results were not
reported to be adjusted for purity, the published results were multiplied by the purity if it was reported to be less than 95%.
-------
Table 5. Bioaccunulation of Tributyltin by Aquatic Organisms
Chemical'
Hardness
(rag/L as
CaOU
Concentration
in Uater (ug/L)tt
Duration
{days)
Tissue
BCF or
BAF1
Reference
00
Rainbow trout
(13.8 g).
Oncorhynchus
mykiss
Rainbow trout
(32.7).
Oncorhynchus
myki ss
Snail (female),
Nucella lopillus
Snail (female),
Nucella lopillus
Blue mussel
(spot),
Hytilus edulis
Blue mussel (adult).
Hytilus edulis
Blue mussel
(juvenile),
Hytilus edulis
TBTO
(97%)
TBTO
(97%)
135
135
TBT
Field
28.5-34.2'
Field
Field
FRESHWATER SPECIES
0.513 64
Whole body
406
Martin et al. 1989
1.026 15
SALTWATER SPECIES
0.0038 to 249 to
0.268 408
0.070 529 to
634
0.24 45
<0.1 60
<0.1 60
Liver
Gall
bladder/bile
Kidney
Carcass
Peritoneal
fat
Gill
Blood
Gut
Muscle
Soft
parts
Soft
parts
Soft
parts
-
_
1,179 Martin et al. 1989
331
2,242
1,345
5,419
1.014
653
487
312
11,000 to Bryan et al. 1987
38,000
17.000 Bryan et al. 1987
6,833' Thain and Ualdock 1985;
Thain 1986
11,000 Salazar and Salazar 1990a
25,000 Salazar and Salazar 1990a
-------
Table 5. (continued)
Species Chemical*
Blue mussel, "
Mytilus edulis
Blue mussel Field
(juvenile),
Hvtilus edulis
Pacific oyster, TBTO
Crassostrea gigas
Pacific oyster, TBTO
Crassostrea gigas
Pacific oyster, "
Crassostrea gigas
Pacific oyster, TBTO
Crassostrea gigas
Pacific oyster, TBTO
Crassostrea gigas
European flat oyster, TBTO
Ostrea edulis
European flat oyster, TBTO
Ostrea edulis
European flat oyster, TBTO
Ostrea edulis
European flat oyster, "
Ostrea edulis
European flat oyster, "
Ostrea edulis
Salinity
(g/kg)
"
28-31.5
28-31.5
28.5-34.2
29-32
29-32
28-31.5
28-34.2
28-34.2
28.5-34.2
28.5-34.2
Concentration
in Water lua/Lf
0.452
0.204
0.204
0.079
<0.105
1.216
0.1460
0.24
1.557
0.1460
1.216
0.24
2.62
0.24
2.62
Duration
(days)
56
84
21
21
45
56
56
21
75
75
45
45
Tissue
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
Soft
parts
BCF or
BAF*
23,000
27,000
10,400
37,500
5.000-
60.000
1.874'
6.047'
7,292'
2.300
11,400
960'
875'
397'
1,167'
192.3'
Reference
Salazar et al. 1987
Salazar and Salazar,
In press
Ualdock et al. 1983
Ualdock et al. 1983
Thain and Ualdock 1985;
Thain 1986
Ualdock and Thain 1983
Ualdock and Thain 1983
Ualdock et al. 1983
Ualdock et al. 1983
Thain 1986
Thain and Ualdock 1985;
Thain 1986
Thain and Ualdock 1985;
Thain 1986
-------
Table 5. (continued)
• TBTO = tributyltin oxide; Field = field study. Percent purity is given in parentheses when available.
° Measured concentration of the tributyltin cation.
c Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured concentrations of TBT in water and tissue.
" Test organisms were exposed to leachate from panels coated with antifouling paint containing tributyltin.
* Salinity (g/kg).
' BCFs were calculated based on the increase above the concentration of TBT in control organisms.
-------
Table 6. Other Data on Effects of Tributyltin on Aquatic Organisms
Hardness
(mg/L as
Species Chemical CaCOO
Alga,
Natural assemblage
Blue-green alga,
Anabaena f I os- aquae
Green alga,
Ankistrodesmus falcatus
Green alga TBTO
Ankistrodesmus falcatus (97%)
Green alga,
Scenedesmus guadricauda
Hydra, TBTO 51.0
Hydra sp. (96%)
Asiatic clam (larva). TBTO
Corbicula f luminea
Cladoceran, TBTO
Daphnia magna
Cladoceran (<24 hr), TBTC 200
Daphnia magna
Cladoceran (<24 hr), TBTO 200
Daphnia magna
Cladoceran (adult), TBTC
Daphnia magna
Rainbow trout TBTO
(yearling),
Oncorhynchus mykiss
Duration
4 hr
4 hr
4 hr
7 days
14 days
21 days
28 days
4 hr
96 hr
24 hr
24 hr
24 hr
24 hr
8 days
24 hr
48 hr
Effect
FRESHWATER SPECIES
ECSO
(production)
ECSO
(production)
ECSO
(production)
(reproduction)
BCF 300
BCF 253
BCF 448
BCF 467
ECSO
(production)
EC50
(clubbed tentacles)
ECSO
LC50
ECSO
(mobility)
ECSO
(mobility)
Altered phototaxis
LC50
Concentration
(UQ/L)'
5
13
20
5
5.2
4.7
2.1
1.5
16
0.5
1,990
3
11.6
13.6
0.45
25.2
18.9
Reference
Wong et al. 1982
Wong et al. 1982
Wong et al. 1982
Naguire et al. 1984
Wong et al. 1982
Brooke et al. 1986
Foster 1981
Roister and Halacha
1972
Vighi and Calamari
1985
Vighi and Calamari
1985
Header 1986
Alabaster 1969
-------
Table 6. (continued)
Hardness
(mg/L as
Species Chemical CaCO,) Duration
Rainbow trout, TBTO - 24 hr
Oncorhynchus mvkiss
Rainbow trout TBTC 94-102 110 days
(embryo, larva).
Oncorhynchus mvkiss
Guppy (3-4 wk), TBTO 209 3 months
Poeci I ia reticulata
Frog (embryo, larva), TBTO - 5 days
Rana temporaria
TBTF
TBTO
TBTF
Effect
EC50
(rheotaxis)
20% reduction
in growth
23% reduction
in growth; 6.6%
mortality
100% mortality
Thymus atrophy
Hyperplasia of kidney
heraopoietic tissue
Marked liver
vacuolation
Hyperplasia of
cornea I epithelium
LC40
LCSO
Loss of body water
Loss of body water
Concentration
(ua/D* Reference
30.8 Chliamovitch and
Kuhn 1977
0.18 Seinen et al. 1981
0.89
4.46
0.32 Wester and Canton 1987
1.0
1.0
10.0
28.4 Laugh I in and Linden 1982
28.2
28.4
28.2
-------
Table 6. (continued)
Salinity
Species Chemical (g/kg)
Natural microbial TBTC 2 and 17
populations
Natural microbial TBTC 2 and 17
populations
Green alga, TBTO 34-40
Dunatiei la tertiolecta
Green alga, TBTO
Dunatiei la sp.
w Green alga, TBTO
Dunaliella sp.
Green alga, TBTO
Dunal iella tertolecta
Diatom, TBTO
Phaeodoctylum
tricornutum
Diatom, TBTO
N i t zsch i a sp.
Diatom, TBTA 30
Skeletonema
costatum
Diatom, TBTA 30
Skeletonema
costatum
Duration Effect
SALTWATER SPECIES
1 hr
1 hr
(incubated
10 days)
18 days
72 hr
72 hr
8 days
72 hr
8 days
72 hr
72 hr
Significant
decrease in
metabol ism of
nutrient substrates
50% mortality
Population growth
Approx. EC50
(growth)
100% mortality
EC50
No effect on
growth
EC50
EC50
(population growth)
LC50
Concentration
(ug/D* Reference
4.454 Jonas et al. 1984
89.07 Jonas et al. 1984
1.0 Beaumont and Newman 1986
1.460 Salazar 1985
2.920 Salazar 1985
4.53 Dojmi et al. 1987
1.460-5.839 Salazar 1985
1.19 Dojmi et al. 1987
0.3097 Walsh et al. 1985; 1987
12.65 Walsh et al. 1985; 1987
Diatom,
Skeletonema costatum
TBTO
34-40
12-18 days
Population growth
1.0
Beaumont and Newman 1986
-------
Table 6. (continued)
Species
Diatom,
Skeletonema
costatum
Diatom,
Skeletonema
costatum
Diatom,
Skeletonema
costatum
Diatom,
Skeletonema
costatum
Diatom,
ui Skeletonema
** costatum
Diatom,
Skeletonema
costatum
Diatom,
Mi nut ocellus
polymorphus
Diatom,
MinutoceUus
polymorphus
Diatom,
Thalassiosira
pseudonana
Diatom,
Thalassiosira
pseudonana
Salinity
Chemical (q/kg) Duration
TBTO 30 72 hr
TBTO 30 72 hr
TBTC 30 72 hr
TBTC 30 72 hr
TBTF 30 72 hr
TBTF 30 72 hr
TBTO - 48 hr
TBTC - 48 hr
TBTA 30 72 hr
TBTO 30 72 hr
Effect
ECSO
(population growth)
LC50
ECSO
(population growth)
LC50
ECSO
(population growth)
LC50
ECSO
ECSO
ECSO
(population growth)
ECSO
(population growth)
Concentration
(ug/L)'
0.3212
13.82
0.3207
10.24
>0.2346,
<0.4693
11.17
-340
-330
1.101
1.002
Reference
Walsh et al. 1985; 1987
Walsh et al. 1985
Walsh et al. 1985; 1987
Walsh et al. 1985; 1987
Walsh et al. 1985; 1987
Walsh et al. 1985
Walsh et al. 1988
Walsh et al. 1988
Walsh et al. 1985
Walsh et al. 1985; 1987
-------
Table 6. (continued)
Salinity
Species Chemical (fl/kg)
Microalga, TBTO 34-40
Pavlova lutheri
Dinof lagellate, TBTO
Gynmodiniun
splendens
Macroalgae, TBT 6
Fucus vesiculosus
Hydroid, TBTF 35
Campanularia f lexuosa
Oogwh inkle (adult). c
Nucella lapillus
Ul
Ul
Blue mussel (larva), TBTO
Mytilus edulis
Blue mussel (larva), TBTO
Mytilus edulis
Blue mussel (spat), c 28.5-34.2
Hytilus edulis
Blue mussel (spat), c 28.5-34.2
Hytilus edulis
Blue mussel (larva), TBTO 33
Mytilus edulis
Blue mussel TBTO 33.7
(juvenile),
Mytilus edulis
Duration
12-26 days
72 hr
7 days
11 days
120 days
24 hr
4 days
45 days
45 days
15 days
7 days
Concentration
Effect (ug/L)'
Population growth 1.0
100% mortality 1.460
Photosynthesis 0.6
and nutrient
uptake reduced
Colony growth 0.01
stimulation;
no growth at 1.0 ug/L
41% Imposex 0.05
(super-imposition
of male anatomical
characteristics on
females)
No effect on sister 1.0
chromatid exchange
Reduced survival *0.1
Significant 0.24
reduction in growth;
no mortality
100% mortality 2.6
51% mortality; 0.0973
reduced growth
Significant 0.3893
reduction in
growth
Reference
Beaumont and Newman 19&
Salazar 1985
Lindblad et al. 1989
Stebbing 1981
Bryan et al. 1986
Dixon and Prosser 1986
Dixon and Prosser 1986
Thain and Ualdock 1985;
Thain 1986
Thain and Ualdock 1985;
Thain 1986
Beaumont and Budd 1984
Stromgren and Bongard 1
-------
Table 6. (continued)
Species
Blue mussel
(juvenile).
Hyti I us edulis
Blue mussel
(juvenile),
Hyti I us edulis
Blue mussel
( juveni le),
My til us edulis
Blue mussel
(juvenile),
Mytilus edulis
m Blue mussel
01 (juvenile),
Mytilus edulis
Blue mussel
(juvenile),
My t i I us edulis
Blue mussel
12.5 to 4.1 cm),
Mytilus edulis
Blue mussel
(2.5 to 4.1 cm),
Mytilus edulis
Scallop (adult),
Hinnites multiruqosus
Pacific oyster (spat),
Crassostrea gigas
Pacific oyster (spat),
Crassostrea gigas
Salinity
Chemical (q/kq)
Field
Study
Field
Study
Field
Study
c
c
c
c
c
c
TBTO
TBTO
Duration
1-2 wk
1-12 wks
1-12 wks
56 days
196 days
56 days
66 days
66 days
110 days
48 days
14 days
Concentration
Effect (ug/L>*
Reduced growth; 0.2
at <0.2 ug/L
environmental
factors most
important
Reduced growth >0.1
Reduced growth
tissue cone. 2.0 ug/g
Reduced condition 0.157
Reduced growth; 0.070
no effect at day 56
of 0.2 ug/L
No effect on 0.160
growth
LC50 0.97
Significant 0.31
decrease in
shell growth
No effect on 0.204
condition
Reduced growth 0.020
Reduced oxygen 0.050
consumption and
feeding rates
Reference
Salazar and Salazar
Salazar and Salazar
In press
Salazar and Salazar
In press
Salazar et al. 1987
Salazar and Salazar
Salazar and Salazar
Valkirs et al. 1985
Valkirs et al. 1985
Salazar et al. 1987
Lawler and Aldrich
Lawler and Aldrich
19901
1
i
1987
1987
,1987
1987
1987
-------
Table 6. (continued)
Salinity
Species Chemical (g/ta)
Pacific oyster (spat), c 28.5-34.2
Crassostrea gigas
Pacific oyster (spat), c 28.5-34.2
Crassostrea gigas
Pacific oyster (spat), TBT
Crassostrea gigas
Pacific oyster (spat), TBTO 29-32
Crassostrea gigas
Pacific oyster (spat). TBTO 29-32
Crassostrea gigas
Pacific oyster (larva), c
Crassostrea gigas
Pacific oyster (larva), c
Crassostrea gigas
Pacific oyster (adult), Field
Crassostrea gigas
Pacific oyster (larva), TBTF 18-21
Crassostrea gigas
Pacific oyster (larva), TBTF 18-21
Crassostrea gigas
Pacific oyster TBTA 28
(embryo),
Crassostrea gigas
Pacific oyster TBTA
(embryo),
Crassostrea gigas
Pacific osyter (Larva), TBTA
Crassostrea gigas
Duration
45 days
45 days
49 days
56 days
56 days
30 days
113 days
-
21 days
15 days
24 hr
24 hr
24 hr
Effect
40% mortality;
reduced growth
90% mortality
Shell thickening
No growth
Reduced growth
100% mortality
30% mortality
and abnormal
development
Shell thickening
Reduced number of
normally developed
larvae
100% mortality
Abnormal develop-
ment; 30-40%
mortality
Abnormal develop-
ment
Abnormal develop-
ment
Concentration
(ua/L>a
0.24
2.6
0.020
1.557
0.1460
2.0
• 0.2
>0.014
0.02346
0.04692
4.304
0.8604
>0.9
Reference
Thain and Ualdock 1985;
Thain and Ualdock 1985
Thain et al. 1987
Ualdock and Thain 1983
Ualdock and Thain 1983
Alzieu et al. 1980
Alzieu et al. 1980
Uolniakowski et al. 1987
Springborn Bionomics 1984a
Springborn Bionomics 1984a
His and Robert 1980
Robert and His 1981
Robert and His 1981
-------
Table 6. (continued)
Salinity
Species Chemical (g/kg)
Pacific oyster (larva), TBTA
Crassostrea g i gas
Pacific osyter c
(150-300 mg)
Crassostrea gigas
Eastern oyster d
(2.7-5.3 cm),
Crassostrea virginica
Eastern oyster d
(2.7-5.3 cm),
Crassostrea virginica
Eastern oyster (adult), c 33-36
Crassostrea virginica
in Eastern oyster (adult), c 33-36
00 Crassostrea virginica
Eastern oyster TBTC 18-22
(embryo),
Crassostrea virginica
Eastern oyster TBTO 11-12
(juvenile),
Crassostrea virginica
Eastern oyster (adult), c
Crassostrea virginica
European flat oyster TBTO 30
(spat).
Ostrea edulis
Duration
48 hr
56 days
67 days
67 days
57 days
30 days
48 hr
96 hr
8 Mks
20 days
Effect
100% mortality
No effect on
growth
Decrease in
condition index
(body weight)
No effect on
survival
Decrease in
condition index
LC50
Abnormal shell
development
EC50; shell
growth
No affect on
sexual development,
fertilization
Significant
reduction in
growth
Concentration
(ug/L)'
2.581
0.157
0.73
1.89
0.1
2.5
0.77
0.31
1.142
0.01946
Reference
Robert and His 1981
Salazar et al. 1987
Valkirs et al. 1985
Valkirs et al. 1985
Henderson 1986
Henderson 1986
Roberts, Manuscript
Walker 1989b
Roberts et al. 1987
Thain and Waldock 1<
European flat oyster
(spat),
Ostrea edulis
28.5-34.2
45 days
Decreased growth
0.2392
Thain and Waldock 1985;
Thain 1986
-------
Table 6. (continued)
Species Chemical
European flat oyster c
(spat),
Ostrea eduiis
European flat oyster c
(adult),
Ostrea eduiis
European flat oyster c
(adult),
Ostrea eduiis
European flat oyster c
(adult).
Ostrea eduiis
European flat oyster c
(140-280 mg)
Ostrea eduiis
Native Pacific oyster c
(100-300 mg)
Ostrea luricla
Ouahog clam TBTO
(embryo, larva),
Hercenaria mercenaria
Clam (adult), c
Hacona nasuta
Ouahog clam TBTO
(veligers),
Hercenaria mercenaria
Ouahog clam TBTO
(post larva),
Hercenaria mercenaria
Ouahog clam (larva), TBTC
Hercenaria mercenaria
Salinity
(q/kq) Duration
28.5-34.2 45 days
28-34 75 days
28-34 75 days
28-34 75 days
56 days
56 days
14 days
110 days
8 days
25 days
18-22 48 hr
Concentration
Effect (uq/D*
70% mortality
Complete inhibition
of larval
production
Retardation of
sex change from
male to female
Prevented gonadal
development
No effect on growth
No effect on growth
Reduced growth
No effect on
condition
Approx. 35%
dead; reduced
growth; £1.0 u/L
100% mortality
100% dead
Delayed develop-
ment
2.6
0.24
0.24
2.6
0.157
0.157
>0.010
0.204
0.6
10
0.77
Reference
Thain and Ualdock 1985;
Thain 1986
Thain 1986
Thain 1986
Thain 1986
Salazar et al. 1987
Salazar et al. 1987
Laughlin et al. 1987;1988
Salazar et al. 1987
Laughlin et al. 1987;1989
Laughlin et al. 1987,-1989
Roberts, Manuscript
-------
Table 6. (continued)
Species
Common Pacific
Littleneck (adult),
Protothaca stamina
Copepod (subadult),
Eurytemora aff inis
Copepod (subadult),
Eurytemora aff inis
Copepod,
Acartia tonsa
Copepod ( naupl i i ),
Acartia tonsa
Copepod ( naupl i i ) ,
Acartia tonsa
Copepod ( naupl i i ) ,
Acartia tonsa
Copepod (adult),
Acartia tonsa
Amphipod (larva,
juvenile),
Gammarus oceanus
Amphipod (larva,
juvenile),
Gammarus oceanus
Amphipod (larva,
juvenile),
Garrmarus oceanus
Amphipod (larva,
juvenile),
Gammarus oceanus
Chemical
TBTO
TBT
TBT
TBTO
TBTC
TBTC
TBTC
TBTO
TBTO
TBTF
TBTO
TBTF
Salinity
(a/kg) Duration
33-34 96 hr
10 72 hr
10 72 hr
6 days
10-12 9 days
10-12 6 days
10-12 6 days
28 5 days
7 8 wk
7 8 wk
7 8 wk
7 8 wk
Concentration
Effect (ug/D*
100% survival
LC50
LC50
EC50
Reduced survival
Reduced survival;
no effect 0.012 ug/L
Reduced survival;
no effect 0.010 ug/L
Reduced egg
production
100X mortality
100X mortality
Reduced survival
and growth
Reduced survival
and increased
growth
>2.920
0.5
0.6
0.3893
>0.029
0.023
0.024
0.010
2.920
2.816
0.2920
0.2816
Reference
Salazar and Salazar,
Manuscript
Bushong et al. 1988
Bushong et al. 1988
UTen 1983
Bushong et al. 1990
Bushong et al. 1990
Bushong et al. 1990
Johansen and Hohlenberg 1987
Laughlin et al. 1984b
Laughlin et al. 1984b
Laughlin et al. 1984b
Laughlin et al. 1984b
-------
Table 6. (continued)
Species
Amphipod,
Gamma r us sp.
Amphipod (adult),
Orchestia traskiana
Amphipod (adult),
Orchestia traskiana
Grass shrimp,
Palaemonetes pugio
Mud crab (larva).
Rhithropanopeus ham' si i
Mud crab (larva),
Rhi thropanopeus harrisii
Mud crab (larva),
Rhithropanopeus harrisii
Mud crab (larva),
Rhithropanopeus harrisii
Mud crab (zoea),
Rh i tropanopeus harrisi i
Mud crab (zoea), FL
Rhithropanopeus harrisii
Mud crab,
Rhithropanopeus harrisii
Mud crab.
Rh i thropanopeus harrisii
Mud crab,
Rhithropanopeus harrisii
Mud crab,
Rh i thropanopeus harrisii
Chemical
TBTC
TBTO
TBTF
TBTO
(95%)
TBTO
TBTS
TBTO
TBTS
TBTO
TBTO
TBTO
TBTO
TBTO
TBTO
Salinity
(fl/kq)
10
30
30
9.9-11.2
15
15
15
15
15
15
15
15
15
15
Duration
24 days
9 days
9 days
20 min
15 days
15 days
15 days
15 days
20 days
40 days
6 days
6 days
6 days
6 days
Effect
No effect
Approx. 80%
mortality
Approx. 90%
mortality
No avoidance
Reduced develop-
mental rate and
growth
Reduced develop-
mental rate and
growth
63% mortality
74% mortality
LC50
LC50
BCF=24 for
carapace
BCF=6 for
hepatopancreas
BCF=0.6 for
testes
BCF=41 for
gill tissue
Concentration
(ug/D*
0.579
9.732
9.732
30
14.60
18.95
>24.33
28.43
13.0
33.6
5.937
5.937
5.937
5.937
Reference
Hall et al. 1988b
Laughlin et al. 1982
Laugh 1 in et al. 1982
Pinkney et al. 1985
Laughlin et al. 1983
Laughlin et al. 1983
Laughlin et al. 1983
Laughlin et al. 1983
Laughlin and French 1989
Laughlin and French 1989
Evans and Laughlin 1984
Evans and laughlin 1984
Evans and Laughlin 1984
Evans and Laughlin 1984
-------
Table 6. (continued)
Species Chemical
Mud crab, TBTO
Rhithropanopeus harrisii
Fiddler crab, TBTO
Uca pugilator
Fiddler crab, TBTO
Uca pugi lator
Fiddler crab, TBTO
Uca pugi lator
Brittle star, TBTO
Oph i oderma brevispina
Atlantic menhaden TBTC
(juvenile),
cr> Brevoortia tvrannus
to
Atlantic menhaden TBTO
(juvenile),
Brevoortia tvrannus
Chinook salmon TBTO
(adult),
Oncorhynchus tshawvtscha
Chinook salmon TBTO
(adult),
Oncorhynchus tshawytscha
Chinook salmon TBTO
(adult),
Oncorhynchus tshawytscha
Mummichog (juvenile), TBTO
Fundulus heteroclitus
Humnichog, TBTO
Salinity
(q/kq)
15
25
25
25
18-22
10
9-11
28
28
28
2
9.9-11.2
Duration
6 days
<24 days
3 weeks
7 days
4 wks
28 days
"
96 hr
96 hr
96 hr
6 wks
20 min
Effect
BCF=1.5 for
chelae muscle
Retarded limb
regeneration and
molting
Reduced burrowing
Limb malformation
Retarded arm
regeneration
No effect
Avoidance
BCF=4300 for
liver
BCF=1300 for
brain
BCF=200 for
muscle
Gill pathology
Avoidance
Concentration
(ua/L)'
5.937
0.5
0.5
0.5
-0.1
0.490
5.437
1.49
1.49
1.49
17.2
3.7
Reference
Evans and Laughlin 1984
Weis et al. 1987a
Ueis and Perlmutter 1987
Weis and Kim 1988;
Weis et al. 1987a
Walsh et al. 1986a
Hall et al. 1988b
Hall et al. 1984
Short and Thrower 1986a
Short and Thrower 1986a
Short and Thrower 1986a
Pinkney 1988; Pinckney et
Pinkney et al. 1985
,1986c
,1986c
,1986c
al. 19
Fundulus heteroclitus
-------
Table 6. (continued)
Salinity
Species Chemical (q/kq)
Inland silverside TBTC 10
(larva),
Henidia beryl Una
California grunion c
(gamete through embryo),
Leuresthes tenuis
Munnichog (embryo), TBTO 25
Fundulus heteroclitus
California grunion c
(gamete through embryo),
Leuresthes tenuis
California grunion c
(gamete through embryo),
Leuresthes tenuis
California grunion c
(embryo),
Leuresthes tenuis
California grunion c
(larva).
Leuresthes tenuis
Striped bass TBTO 9-11
(juvenile). (95X)
Morone saxati I is
Speckled sanddab TBTO 33-34
(adult),
Chi tharichthys stigma eus
Duration
28 days
10 days
10 days
10 days
10 days
10 days
7 days
~
96 hr
Concentration
Effect (uq/L)'
Reduced growth 0.093
Significantly 0.14-1.71
enhanced growth
hatching success
Teratology 30
Significantly 0.14-1.72
enhanced growth
and hatching
success
50% reduction 74
in hatching
success
No adverse 0.14-1.72
effect on
hatching success
or growth
Survival 0.14-1.72
increased as
concentration
increased
Avoidance 24.9
LC50 18.5
Reference
Hall et al. 1988b
Newton et al. 1985
Ueis et al. 1987b
Newton et al. 1985
Newton et al. 1985
Newton et al. 1985
Newton et al. 1985
Hall et al. 1984
Salazar and Salaza
Manuscript
Fouling communities
33-36
2 months
Reduced species
and diversity;
no effect at 0.04 ug/L
0.1
Henderson 1986
Fouling communities
126 days
No effect
0.204
Salazar et al. 1987
-------
Table 6. (continued)
* TBTA = tributyltin acetate; TBTC = tributyltin chloride; TBTF = tributyltin fluoride; TBTO = tributyltin oxide;
TBTS = tributyltin sutfide. Percent purity is given in parentheses when available.
" Concentration of the tributyltin cation, not the chemical. If the concentrations were not measured and the published results were not
reported to be adjusted for purity, the published results were multiplied by the purity if it was reported to be less than 95X.
c The test organisms were exposed to leachate from panels coated with antifouling paint containing tributyltin.
The test organisms were exposed to leachate from panels coated with antifouling paint containing a tributyltin polymer and
cuprous oxide. Concentrations of TBT were measured and the authors provided data to demonstrate the similar toxicity of a
pure TBT compound and the TBT from the paint formulation.
cn
-------
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