67l6/88
AMBIENT WATER QUALITY CRITERIA FOB TRIBUTYLTIN - 1988
Prepared b7
Center Tor Lake Superior Environmental Studies
University of Wisconsin-Superior
Superior, VI 54880
Prepared for
U.S. Environmental Protection Agency
Office of Research and Development
Environmental Research Laboratories
Duluth, MN
N&rrag&nsett, Rhode Island
Prepared through
Battelle Memorial Research Institute
505 King ftvenue
Columbus. OH 43201
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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 distribution.
Mention of trade names or commercial products does not constitute endorsement
or recommendation for use.
This document is available to the public through the Criteria and Standards
Division, Office of Water Regulations and Standards, U.S. EPA, Washington. DC
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FOREWORD
The Criteria and Standards Division of the Office of Water Regulation^
and Standards has instituted water quality advisories as a vehicle for
transmitting the best available scientific information concerning the aquatic
life and human health effects of selected chemicals in surface waters
Advisories are prepared for chemicals for which information is needed quicklv
but for which sufficient data, resources, or time are not available to allow
derivation of national ambient water quality criteria.
Data supporting advisories are usually not as extensive as required for
derivation of national ambient water quality criteria, and the strength of an
advisory will depend upon the amount, type, and reliability of the data
available We feel, however, that it is in the best interest of all concerned
to make the enclosed information available to those who need it.
Users of an advisory should take into account its basis and intended
uses. Anyone who has additional information that will supplement or
substantially change an advisory is requested to make the information known to
us. An advisory for an individual chemical will be revised if any significant
and valid new data make it necessary.
We invite comments to help improve this product.
Edmund M. Notion, Director
Criteria and Standards Division
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ACKNOWLEDGMENTS
Larry T Brooke Robert Scott Carr
(freshwater contributor) (saltwater contributor)
University of Wisconsin-Superior Battelle Ocean Sciences
Superior, WI 54880 Duxbury, Massachusetts
Anthony R. Carlson David J. Hanson
(document coordinator) (saltwater coordinator)
Environmental Research Laboratory-Duluth Environmental Research Laboratory
Duluth, MN 55804 Narragansett. Rhode Island
Clerical Support: Shelley A. Heintz
IV
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CONTENTS
Page
Foreword . . ... i 11
Acknowledgments . . . iv
Tables ... vi
Introduction 1
Background Information . 3
Acute Toxicity to Aquatic Animals 4
Chronic Toxicity to Aquatic Animals 6
Toxicity to Aquatic Plants 8
Bioaccumulation 9
Other Data 10
Unused Data 13
Summary 15
Aquatic Life Advisories 16
References 46
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TABLES
Page
1 Acute Toxicity of Tributyltin to Aquatic Animals ... 18
2 Chronic Toxicity of Tributyltin to Aquatic Animals . . 24
3 Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios . 26
4. Toxicity of Tributyltin to Aquatic Plants 30
5. Bioaccumulation of Tributyltin by Aquatic Organisms 32
6. Other Data on Effects of Tributyltin on Aquatic Organisms . . 34
VI
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1ntroduction
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 TBT
is a cation whose formula is (C^Hg^Sn*. In sea water TBT exists
mainly as a mixture of the chloride, the hydroxide, the aquo complex, and the
carbonate complex (Laughlin et al. I986a).
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 species 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 tributyltin (Hall and Pinkney 1985;
Laughlin and Linden 1985; Laughlin et al. 1985).
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, and it is this use that will probably contribute most
significantly to direct release of organotins into the aquatic environment
(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
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reduce maximum speed and increase fuel consumption. According to the U.S.
Navy (1984), use of TBT paints would not only reduce fuel consumption by 15%
but would also increase tine between repainting from less than 5 years to 5 Co
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. I986a).
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 (Corbin 1976).
The solubility of tributyltin oxide in water was reported to be 750 ng/L at
a pH of 6.6 and 31.000 /jg/L at a pH of 8.1 (Maguire et al. 1983). The
carbon-tin covatent 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).
TBT readily sorbs to sediments and suspended solids and can persist there
(Cardarelli and Evans 1980). The half-life for desorption of TBT from
sediments was reported to be greater than ten months (Maguire and Tkacz
1985). TBT had a half-life of about 16 weeks in a freshwater sediment
(Maguire and Tkacz 1985) and 23 weeks in a saltwater sediment (Seligman et al
1986).
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
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fungi only under aerobic conditions and only when a secondary carbon source
was supplied. Maguire et al (1984) reported that a 28-day culture of TBT with
Che 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 The major metabolite of TBT in saltwater crabs, fish
and shrimp was dibutyltin (Lee 1986).
Elevated TBT concentrations in fresh and salt waters are primarily
associated with harbors and marinas (Cleary and Stebbing 1985; Hall et al.
1986: Maguire 1984.1986; Maguire and Tkacz 1985; Maguire et al. 1982; Salazar
and Salazar 1985b; Seligman et al. 1986; Unger et al. 1986; Valkirs et al
1986; Waldock and Miller 1983) In some cases the microlayer surface of the
water contained a much higher concentration of TBT than the water column.
Gucinski (1986) suggested that this enrichment of the surface microlayer might
increase the bioavailabi1ity of TBT. No organotins were detected in the
muscle tissue of feral chinook salmon caught near Auke Bay, Alaska, but
concentrations as high as 900 MgAg were reported in muscle tissue of
chinook salmon held in pens treated with TBT (Short and Thrower 1986a).
Only data generated in toxicity and bioconcentration tests on TBTC
(tributyltin chloride), TBTF (tributyltin fluoride). TBTO (bis(tributyltin)
oxide, commonly called "tributyltin oxide") and TBTS (bis(tributyltin)
sulfide, commonly called "tributyltin sulfide") were used in the derivation of
the water quality advisory concentrations for aquatic life presented herein.
All concentrations from such tests are expressed as TBT, not as tin and not as
the chemical tested. 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 Guidelines, and the response to public comment (U.S. EPA 1985a) is
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necessarv in order to understand the following text, tables, and
calculations Results of such intermediate calculations as recalculated LCSOs
and Species Mean Acute Values are given to four significant figures to prevent
roundoff error in subsequent calculations, not to reflect the precision of the
value The latest comprehensive literature search for information for this
document was conducted in May 1988.
Xcute Toxicitv 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 nine freshwater species and range from 0.5 for a hydra, Hydra
sp.. to 227.4 jug/L for a mosquito, Culcx sp. The 96-hr LC50 of
227 4 /jg/L reported by Foster (1931) for the bluegill greatly exceeds all
other acute values, including those for three other species of fish. Foster's
48-hr EC50 for Daphnia magna is also much higher than the results of the two
other acute tests with this species. Therefore, it seems inappropriate to use
the results reported by Foster (1981) in the calculation of the freshwater
Final Acute Value.
Freshwater Species Mean Acute Values (Table 1) were calculated as
geometric means of the available acute values, and then Genus Mean Acute
Values (Table 3) were calculated as geometric meana of the Species Mean Acute
Values. Of the eight freshwater genera for which mean acute values are
available, the most sensitive genus, Hydra, is 20 times more sensitive than
the most resistant, Culex. The four most sensitive genera include a hydra.
two fishes, and an amphipod. The freshwater Final Acute Value for TBT was
calculated to be 0 2972 fig/L using the procedure described in the
Guidelines and the Genus Mean Acute Values in Table 3. This Final Acute Value
is lower than the lowest freshwater Species Mean Acute Value.
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Tests of the acute toxicity of TBT to resident North American saltwater
species that are useful for deriving water quality advisory concentrations
have been performed with 16 species of invertebrates and three species of fish
(Table 1) The 96-hr LC50 of O.OU68 ng/L reported by Becerra-Huencho
U984) for post larvae of the hard clam, Mercenaria mercenana, also kno*n as
che quahog clam, was not used in the derivation of the mean acute value for
this species because results of other studies with embryos, larvae, and post
larvae of the hard clam (Tables 1 and 6) cast doubt on this LC50 For
example. Roberts (Manuscript) reported 48-hr LCSOs of 1.13 /jg/L for embryos
and 1 65 jug/L for larvae of the hard clam. Laughlin et al. (Manuscript)
observed about 35% mortality of larval hard clams exposed for eight days to
0 6 ng/L and reduced growth after 14 days in 0.025 Mg/L- They found
that post larvae were more resistant than larvae; concentrations £ 7.5 (Jg/L
did not reduce survival after 25 days, but 10 ^g/L caused 100% mortality.
Results from these tests, in which concentrations of TBT were measured, differ
markedly from the LC50 of 0.01466 jjg/L that was obtained in a test in which
the concentrations were not measured. The LC50 reported by Becerra-Huencho
(1984) appears to be low because all other data for embryo, larval, and
post-larval clams, mussels, and oysters indicate that acutely lethal
concentrations are in the range of 0.6 to 4.0 /ig/L.
Except for the LC50 reported by Becerro-Huencho (1984), the range of acute
toxicity to saltwater animals is a factor of about 670. Acute values range
from 0.42 /ig/L for juveniles of the mysid, Acanthomysi3 sculpta {Davidson
et al. 1986a,b) to 282.2 jjg/L for adult Pacific oysters, Crassostrea gigas
(Thain 1983). The 96-hr LCSOs for three saltwater fish species range from
1.460 ng/L for juvenile chinook salmon, Oncorhynchus tshawvtscha (Short and
Thrower 1986b) to 23.36 m/L for adult mummichogs, Fundulus heteroclitus
(EG&G Bionomics 1976).
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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 ng/L, whereas the value for adults was
232,2 ng/L (Thain 1983) In renewal tests, the 96-hr LCSOs for larval and
adult blue mussels, Vtvtitus eduhs. were 2.238 and 36.98 /ug/L, respectively
(Thain 1983) Juveniles of the crustaceans Acanthomvsis sculpta and
Metamvsidopsis elongata were slightly more sensitive to TBT than adults
(Davidson et al. 1986a.b; Valkirs et al. 1985; Salazar and Salazar,
Manuscript).
Genus Mean Acute Values are available for 18 saltwater genera and range
from 0.61 //g/L for Acanthornvsis to 204.4 ptg/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 four species of molluscs,
six species of crustaceans, and two species of fish. The saltwater Final
Acute Value for TBT was calculated to be 0.5313 Mg/L (Table 3), which is
lower than the lowest saltwater Species Mean Acute Value.
Chronic Toicictty to Aquatic Animals
The available data that are usable according to the Guidelines concerning
the chronic toticity of TBT are presented in Table 2. Brooke et al. (1986)
reported that the survival of Daphnia magna was 40% at a TBT concentration of
G.5 MgA, and 100% at 0.2 ^ig/L. The mean number of young was reduced
30% by 0.2 /Jg/L, and was reduced 6% by O.I ng/L. The chronic value for
Daphnia magna was calculated to be 0.1414 pg/L, and the acute-chronic ratio
was 30.41.
In an early life-stage test with the fathead minnow, Pimephales promelag.
all fish exposed to 2.20 ug/L died during the test (Brooke et al. 1986).
Survival was reduced by 2% at a TBT concentration of 0.92 ng/L, but was
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higher than in the controls at 0.45 pg/L and lower concentrations. The
mean weight of the surviving fish was reduced 4% at 0.08 /ig/L. 9% at
0 15 pg/L, 257. at 0.45 ng/L. and 48% at 0.92 jug/L. The mean biomass
at the end of the test was higher at 0 08 and 0 15 ng/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 and
the mean biomass increased at 0.08 and 0.15 pg/L, the chronic limits are
0 15 and 0 45 jJg/L. Thus the chronic value is 0.2598 ng/L and the
acute-chronic ratio is 10.01.
Life-cycle toxicity tests have been conducted with the saltwater mysid.
Acanthomvsis sculpta (Davidson et al. 1986a,b) and the sheepshead minnow,
Cvprinodon variegatus (Ward et al. 1981). The effects of TBT on survival,
growth, and reproduction of A. sculpta were determined in four separate tests
lasting from 28 to 63 days. The number of juveniles released per female at a
TBT concentration of 0.19 ng/L was 50% of the number released in the
control treatment, whereas the number released at 0.09 M8/L was higher than
in the control treatment The data concerning the effects of TBT on survival
and growth are not easy to interpret. At concentrations from 0.08 to
0.27 MgA. survival and weight were sometimes equal to or better than in
the control treatment, but at concentrations of 0.38 pg/L and above,
survival and weight were always reduced by at least 23%. The chronic value is
0 1308 ng/L, and the acute-chronic ratio is 4.664 (Table 2).
In the life-cycle test conducted with the estuarine fish Cvprinodon
van eeatus (Ward et al. 1981), mean measured concentrations were 240 to 300%
of the nominal concentrations in the first 34 days and 45 to 112% of nominals
in the remainder of this 177-day test. In the same publication, measured
concentrations were 18 to 32% of nominals during a 21-day lethality test and
80% of nominal during a bioconcentration test. No data were used from this
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publication because the various ratios of the measured and nominal concen-
trations of TBT in the different tests suggest that problems existed in the
delivery of TBT or in the analytical chemistry or both.
The Final Acute-Chronic Ratio of 11 24 was calculated as the geometric
mean of the acute-chronic ratios of 30 41 for Daphnia magna. 10.01 for
Pimejahales oromelas. and 4 664 for Acanthomysis scujjtta. Division of the
freshwater and saltwater Final Acute Values by 11,24 results in freshwater and
saltwater Final Chronic Values of 0.02844 and 0.04727 ftg/L, respectively
(Table 3). Both of these Final Chronic Values are below the eiperimenrally
deternuned chronic values
Unacceptable effects on commercially important saltwater molluscs occurred
at TBT concentrations less than 0.04727 jjg/L (Table 0). Growth or
development of the Pacific oyster. European flat oyster, and hard clam was
reduced at 0.023, 0 019, and 0.025 ftg/l. respectively. A TBT concentration
of 0.047 pg/L was lethal to larval C. gigas. Because adverse effects on
important saltwater species have been documented to occur at concentrations as
low as 0.019 pg/L, the saltwater Final Chronic Value is lowered to
0.010 ng/L to adequately protect these important species.
Toxicitv to Aquatic Plants
Planck 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 1,762 ;tg/L, but moat were between 1QQ and 250 ;ig/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, Punattell a sp.; the diatoms,
Phaeodactvlum tri eornutum. Skeletonema costatum. and Thallassiosira
pseudonana: and the dinof1agellate, Cvmnodiniufn solendens (Tables 4 and 6)
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The 14-day EC50 of 0.06228 jig/L for S. costatum (EG4G Bionomics 198lc) was
Che lowest value reported, but Thain (1963) reported that a measured
concentration of 0.9732 pg/L was algistatic to the same species (Table 4).
The 72-hr ECSOs based on population growth ranged from approximately 0 3 to
> 5.8 fig/L (Table 6) Lethal concentrations were generally more than an
order of magnitude greater than ECSOs and ranged from 1.460 to 13.82 pg/L.
Identical tests conducted on tributyltin acetate, tributyltin chloride,
tributyltin fluoride, and tributyltin oxide with S. costatum resulted in ECSOs
from 0.2346 to 0.4693 /jg/L and LCSOs from 10.24 to 13.82 pg/L (Walsh et
al. 1985).
& 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. However, the available data indicate that freshwater
and saltwater plants will be protected by concentrations that adequately
protect freshwater and saltwater animals.
Bioaccumulation
Maguire et al. (1984) obtained bioconcentration factors (BCF) of 253 to
467 with the freshwater green alga, Ankistrodesmus falcatus (Table 5).
The extent to which TBT is accumulated by saltwater animals in tests
lasting 28 days or more has been investigated with three species of bivalve
molluscs (Table 5). Thain and Wai dock (1985) reported a BCF of 6,833 for the
soft parts of blue mussel spat exposed to 0.24 jig/L for 45 days.
The highest BCF reported for a saltwater species was 11,400 for the soft parts
of the Pacific oyster exposed to a TBT concentration of 0.1460 fjg/L for 56
days (ffaldock and Thain 1983). A BCF of 6,047 was observed for the soft parts
of the Pacific oyster exposed to 0.1460 ng/L for 21 days (Waldock et al.
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1983). The lowest steady-state BCF reported 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 pg/L for 45 days (Thatti 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
\ddit\onil data on the \eth*V and sublethal effects of TBT on aquatic
species are-presented in Table 5. Foster (1981) reported a 24-hr EC50 of
1,990 fig/L for larvae of the claa, Corbicula fluminea. This value is much
higher than the acute values reported by Foster (1981) for Daphnia magna and
the bluegill. which were themselves considered unusually high. Meador (1986)
reported that a TBT concentration of 0.45 jig/I affected the behavior of
Daphnia magna in an 8-day test. Exposures of 24 and 48 hr resulted in LCSOs
of 25.2 and 18.9 Mg/L *»th rainbow trout, Salmo gairdneri (Alabaster
1969). Seinen et al. (1981) exposed rainbow trout to 0.18 fig/L for 110
days and observed a 20% reduction in growth. Laughlin and Linden (1982) found
little difference in the toxicities of TBTF and TBTO to embryos and larvae of
the frog, Rana temporaria.
The most unusual effect of TBT on saltwater animals is the superimposiCion
of male characteristics on female stenoglossan gastropoda. This phenomenon.
termed "imposes," can result in females with a penis, a duct leading to a
deferens, and the convolution of the normally straight oviduct (Smith 1981)
Exposure of N. lapil tus to 0.05 /jg/L in a laboratory for four months
produced a 41% incidence of imposes (Bryan et al. 1986). Laboratory tests
with N. obsoletus and two TBT formulations also resulted in imposex but
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exposure conditions were not stated (Smith 1981). TBT has been linked to
imposex in field populations of Nucella lapiI lus. Vassarius obsoletus.
N'assarius reticulatus. and Ocenebra ermacea (Bryan et al 1986, Durchon 1982.
Smith 1981). Imposex has been associated with reduced reproductive capacity
and altered density and population structure in field populations of V
lapiIlus (Bryan et al 1986} but not of N. obsoletus (Smith 1981) Transfers
of snails between clean sites and marinas contaminated with TBT demonstrated a
relationship between the degree of imposex and the concentration of TBT in
tissue, which suggested that snails exposed to as little as 0.0024 /ig/L
might be affected (Bryan et al 1986)
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 pg/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 Aig/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. Mvtilua edulis. exposed to 0.0973 pg/L
was 51%; survivors were moribund and stunted (Beaumont and Budd 1984). 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; Vatkira et al. 1985). The
66-day LC50 for 2.5 to 4.1 cm blue mussels was 0.97 ug/L (Valkirs et al.
1985,1987). Growth of hard clams from fertilization to metamorphosis was
reduced by 0.025 ug/L (Laughlin et al Manuscript). The number of larvae
of the Pacific oyster, Crassostrea giaas. that developed and the number of
spat that set were reduced in 21-day exposures to 0.02346 /ig/L (Springborn
Bionomics I984a). Alzieu et al (1980) reported 30% mortality and abnormal
shell thickening among Pacific oyster larvae exposed to 0.2 ug/L for 113
11
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days. Abnormal development was also observed in exposures of embryos Tor 24
hours or less to TBT concentrations > 0.8604 ng/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 vg/L for 56 days.
Abnormal shell development was observed in an exposure to 0.77 ng/L that
began with embryos of the eastern oyster, Crassostrea vi rginica. and lasted
for +8 hours (Roberts, Manuscript). Adult eastern oysters were also sensitive
to TBT with reductions in condition index after exposure for 57 days to
> 0.1 ng/l (Henderson 1986; Valkirs et at. 1985). Thain and Waldock (1985)
observed a significant reduction in growth of small spat of the European flat
oyster, Ostrea eduli s. exposed for 20 days to a TBT concentration of
0.01946 /ig/L. Growth of larger spat was marginally reduced by
0.2392 MgA (Thain 1986; Thain and Waldock 1985).
Long-term exposures have been conducted with a number of saltwater
crustacean species. Davidson et al. (I986a.b), 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 > 0.2818 fig/I (Laughlin
et al. I984b). Developmental rates and growth of larval mud crabs.
Rhithropanopeus harri sii. were reduced by a 15-day exposure to .>
14.60 Mg/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).
Exposure of embryos of the California grunion, Leuresthes tenuis. for ten
days to 74 ng/L caused a 50% reduction in hatching success (Newton et al.
1985). At TBT concentrations between 0.14 and 1.72 pg/L, growth, hatching
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success, and survival were significantly enhanced. Juvenile Atlantic
menhaden, Brevoortia tvrannus. avoided a TBT concentration of 5.437
and juvenile striped bass. Morone sa^ati 1 is. avoided 24.9 ng/L (Hall et al.
1984) BCFs were 4.300 for liver, 1.300 for brain, and 200 for muscle tissue
of chinook salmon, Qncorhvnchus tshawvtscha. exposed to 1.490 ng/L for 96
hours (Short and Thrower I986a,c)
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. 1984,1966a,b; de Sousa and Pautini
1970; Fnck and DeJimenez 1964; Hopf and Muller 1962; Nishuichi and Yoshida
1972. Ritchie et al 1964; Seiffer and Schoof 1967; Sniff et al. 1975; Tsuda
et al 1986; Upatham 1975; Upatham et al. 1980a.b; Webbe and Sturrock 1964)
Alzieu (1986), Cardarelli and Evans (1980), Cardwell and Sheldon (1986),
Cardwell and Vogue (1986). Champ (1986), Chau (1986). Envirosphere Company
(1986), Good et al. (1980). Guard et al. (1982), Hall and Pinkney (1985).
Hodge et al. (1979). International Joint 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), Seligman et al. (1986), Slesinger and
Dressier (1978). Stebbing (1985), Thayer (1984), Thompson et al. (1985), U S
EPA (1975,19856), U.S. Navy (1984). Valkirs et al. (1985). von Rumker et al
(1974), and Walsh (1986) compiled data from other sources.
Results were not used when the test procedures, test material, or results
were not adequately described (e.g., Chau et al. 1983; Danil'chenko and
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Buzinova 1982; de la Court 1990: Deschiens 1968; EGicG Bionomics 198lb: Filenko
and Isakova 1980; Holwerda and Herwig 1986; Kolosova et al. 1980; Laugh!in
1983, Lee 1985; Nosov and Koloaova 1979, Stroganov et al. 1972.1977) 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 ec al. 1984). The 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 LCSO.
Data were not used when TBT was a component of a formulation, mixture,
paint, or sediment (Cardarelli 1978; Deschiens and Floch 1970; laughlin et al
1982; Maguire and Tkacz 1985; North Carolina Department of Natural Resources
and Community Development 1983; Pope 1981; Quick and Cardarelli 1977; Salarar
and Salazar I985a,b; Santos et al. 1977; Sherman 1963; Sherman and Hoang 1981;
Sherman and Jackson 1981; Walker 1977; Weisfeld 1970), unless data were
available to show that the toxicity was the sane as for TBT alone.
Data were not used when the test organisms were infested with tapeworms
(e.g., Knath 1970). Mottley (1978) 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 L9B2). Tests conducted with too few test organisms were not used (e.g.,
EG&G Bionomics 1979; Good et at. 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 lS84b; Stephenson et al. 1986; ffard et
al. 1981). BCFs were not used when the concentration of TBT in the test
solution was not measured (Laughlin and French, Manuscript; Laughlin et al.
19866).
-------
Summary
The acute toxicity values for eight freshwater animal species range from
0 5 ng/L for a hydra to 10.2 pg/L for a mosquito. Chronic toxicity tests
have been conducted with two freshwater animals Reproduction of Daphnia
was reduced by 0.2 ng/L. but not by 0 1 ng/L, and the acute-chronic
ratio was 30.41 Weight of fathead minnows was reduced by 0.45 fig/L, but
not by 0 15 pg/L, and the acute-chronic ratio for this species was 10.01
Growth of thirteen species of freshwater algae was inhibited by concentrations
ranging from 56.1 to 1.782 ng/L.
Acute values for 19 species of saltwater animals range from
0.61 /ig/L for th« mysid, Acanthomvsia sculota. to 204.4 ng/L for adult
European flat oysters, Ostrea edulis. Acute values for the eleven most sen-
sitive 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,
Acanthomvsis sculota. The chronic value for A. sculpta was 0.1308 pg/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 eieas. Imposes, which is the superimposition
of male characteristics on female stenoglossan gastropods, occurred among
Nucella laoiIlus exposed to 0.05 /ig/L in the laboratory and might occur in
field-exposed snails at 0.0024 ng/L. For some species of snails imposes has
been associated with reduced reproductive potential and population density,
particularly in the vicinity of marinas. Growth or development was reduced at
0.023 tig/I for Crassostrea gigas. 0.019 ng/L for Ostrea
eduli s. and 0.025 fig/L for Mercenaria mercenaria. A TBT concentration of
0.047 yg/L was lethal to larval C. gigas.
IS
-------
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 0264 ng/L more than once every three years on the average
and if the one-hour average concentration does not exceed 0.149 pg/L more
than once every three years on the average.
The procedures described in the "Guidelines for Deriving Numerical
Vational 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 pg/L more than once every three years on the average
and if the one-hour average concentration does not exceed 0.28S ng/L more
than once every three years on the average.
Implementation
&s discussed in the Water Quality Standards Regulation (U.S. EPA 1983a)
and the Foreword to this document, a water quality criterion for aquatic life
has regulatory impact only after it has been adopted in a state water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the U.S
EPA, states designate one or more uses for each body of water or segment
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA
1983b,1987). In each standard a state may adopt the national criterion, if
one exists, or if adequately justified, a site-specific criterion.
IS
-------
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 how
rapidly some aquatic species react to increases in the concentrations of some
pollutants, and "three years" is the Agency's best scientific judgment of the
average amount of time aquatic ecosystems should be provided between
excursions (Stephan et al. 1985; U.S. EPA 1985c). However, various species
and ecosystems react and recover at greatly differing rates. Therefore, if
adequate justification is provided, site-specific and/or pollutant-specific
concentrations, durations, and frequencies may be higher or lower than those
given in national water quality 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 I985c, 1987)
17
-------
Table I Acute Toiieily al Tnbutyltie la Aquatic Aeiarals
oo
Species Met bad*
Hydro. S. y
Hydra sp
Annelid (9 ng). f. U
Lumbricul us voriegotus
Cladoceran. S, U
Dophnio noano
Cladoceran (adult). S. U
Dophnio aaano
Cladoceran (<24 hr). (. U
Pophnio agqno
Aoiphipod. f. *
Connor us oseudol ianaeus
Mosquito (larva). S. M
Cule» sp
Raiobov Irout (juvenile). f. H
So lao ggirdneri
fat head ainooi (juvenile), f. U
Piaapbales prone las
Channel catfish f. H
( juveni le) .
Ictolurus ounctolus
Bluegill. S. U
1 .. pnmi s mo croc lii rui
Hgrdeess LC50
(•g/L as ar CC50
Cbe.icelb C«COT) Ifia/Llc
FBtSHWATtB SPECIES
TBTO 51 0 05
(961)
TBTO 51 8 54
(96X)
TBTO - 66 3d
TBTC - 5 26
TBTO 51 5 43
(96Z)
TBTO 51 8 37
(961)
TBTO 51 5 10 2
(96X)
TBTO 50 6 39
(96Z)
TBTO 51 5 26
(96Z)
TBTO SI 8 55
(96Z)
TBTO - 227 «d
Species Heae
Acute Value
(jia/Lt
0 5
5 4
-
-
4 3
3 7
IQ 2
3 9
2 6
S 5
-
Reference
Brooke et al 1986
Brooke et al 1986
foster I9BI
Ueador 1986
Brooke et ol 1986
Brooke et al 1986
Brooke el al 1986
Brooke «t ol 1986
Brooke et al 1986
Brooke «t al 1986
1981
-------
Table I (coetieued)
Species
Hotbed" Chemical'
Polychaete (juvenile). S. U
Neanthes arenacaodentata
Polychoete (adult). S. U
Neanthes arenaceadentata
Blue aussel (larva). R. -
Hvtilus edulis
Blue mussel (adult). 8. -
Hvlilus edulis
Blue mussel (adult). S. U
Mvtilus edulis
Pacific oyster (larva). R. -
Crossestreo oigos
Pacific oyster (adult). R. -
trossostreo qiaos
Coslera oyster (embryo). S. U
Crassastrea virainico
(astern oyster (embryo). R. U
Crassostrea virainica
TBTO
TBTO
TBTO
TBTO
TBTO
TBTO
TBTO
TBTO
(95X)
TBTC
(astern oyster (embryo). R. U
Crassostreo virainico
TBTC
Salinity
(a/tot
SALTVATCi SPECIES
13-34
33-34
-
-
33-34
-
-
22
18-22
18-22
LC50 Species Mean
or EC50 Acute Valve
(,ia/L»e (ua/Lt
6 812
21 4le 6 812
2 238
36 98*
34 06* 2 238
1 557
282 2* 1 557
0 8759
1 30
0 71
Reference
Salatar and Salazar.
Manuscript
Salazar and Salazar.
Manuscript
Ihain 1983
(ham 1983
Salazar and Salazar.
Uanuscn pt
Thain 1983
Thain 1983
[GIG Biononics
1977
Roberts, yanuscript
Roberts, yanuscript
-------
Table I (continued)
Spec i es
[astern oyster
Cr ossostrea virainica
European flat oyster
(adult).
Os tr ea edul is
Herd clam
(post larnj),
Hercenana «ercenar I o
Hard clam (eoibryo) .
Mercenoria aercenafia
Herd clan (larva).
t>J Mercenaria oerceoaria
O -
Copepod (juvenile),
Curvlenor« effijils
Copepod (adult).
*cart la louse
Copepod (adult).
Hitocra Sfiaioes
Copepad (adult).
Hiiacr a spinipes
Mysid (juvenile).
Aconthomvsis scul Die
Salinity
Method" Cbe«iealU fa/ka)
R. U TBTC 18-22
8. - TBTO
S. U TBTC
R. U TBTC 16-22
R. U TBTC 18-22
F. 11 TBTC IQ 6
«. U TBTO
(951)
S. U TBTT 7
S. U TBTO 7
R. U f
LC50 Species Mean
or [C50 Ac.te Value
|uo/l»c fua/Lt
1 96B 0 9116
204 4 2U4 4
0 OI46641
1 11
1 65 1 165
22 22
0 6126 0 6126
1 877
1 946 1 91 1
0 42
Reference
Roberts. Manuscript
Thain 1981
Secerra-Hnencdo 1984
floberl-s. Uamsirip!
Roberts. Uanuscnpt
Hall e* el 1987
U'ren 1981
Linden et al 1979
Linden el at 1979
Davidson el ol 1 986o
Uysid (juvenile).
ftconlhonnsts scul nta
r. u
0 61
l/oll.rs et al 1965
-------
Table I. (continued)
Sal iaity
Species Method0 Chee>icalb (g/ka)
Uysid (adult). f. U f
Aconthomvsis sculpto
yysid (juvenile). S. U TBTO 33-34
Metamvsidopsis elonqoto
Uysid (subodult). S. U TBTO 33-34
Metomvsidopsis elongoto
Uysid (adult). S. U TBTO 33-34
Metemysidopsis elonqoto
Uysid (adult). S. U TBTO 33-34
UelomvsidoDsis elcnaoto
Aaphipod (adult). R. H TBTO 30
Orchestic troskiono
Anphipod (adult). R. U TBTf 30
Orchestic troskiana
American lobster (larva). R. U TBTO 32
Honiorus oner I c onus
Shore crab (larva). R. - TBTO
Corcinus acenas
Vud crab (larva). R. U TBTS IS
Rhi throoonopeus herrisi i
LC50 Species Heaa
or CCSO Acute Value
(ua/L)c (ua/Ll
1 66* 0 61
<0 9732
1 946a
6 812*
2 433* <0 9732
>I4 609
>I4 089 >I4 60
1 745^ 1 745
9 732 9 732
34 909
Reference
Volkirs et al 1985
Salaiar and Salazar.
Manuscript
Salazar and Salazar.
Manuscript
Salazar and Salazar,
Manuscn pt
Salazar and Salazar.
Manuscn pt
Laughl in et al 1982
Laughl in et al 1 982
Laughlin and French I960
Thoin 1983
Laughl in et al 1983
Mud crab (larva).
Rhithroponopeus harrisii
R. U
TBTO
15
>24 39
34 90
Laughlin et al 1983
-------
Table I. (coetieued)
Species Method*
Shore crab (larva). R. U
Heaiqrapsus nudus
Chemical*
TBTO
Selieit*
U/tal
32
LC50
or CCSO
83 2B»
Species Mean
Acute Vain*
(na/Ll
8J 28
•eference
Laugh!in and Trench 1980
ro
ro
Sheepsheod ainnoi S, U
(juvenil«),
Cyprinodon vorienotus
Sheepsheod uinno* S. U
(juveeile).
C»pfiaodon vorieootus
Sheepsheod mono* S. U
(juveai)•).
Ctprmodoe voriegotus
Sheepshead Biano* (. U
(Jl-49 o»),
C»prinodoa »arieaatus
yuaaiichag (adyll). S. U
fundulus haterocli tus
Cbiaoak sal BOB (juvenile), S. U
Oncorh^ocbus tsha»»tscho
TBTO
TB10
TBTO
TBTO
TBTO
(951)
TBTO
20
20
20
28-32
25
28
16 54
16 54
12 65
2 315*
21 36
I 460
2 315
23 36
I 460
CC1C Bionomcs 1979
CG4C Bionooics 1979
CGIC Bionomics 1979
[CtC Bionomics !9Bld
CC4C Bionomics 1976
Short ond Throier I986b
0 S = static. R = reneial. f = (laa-thraugh. U > ••osured, U = uneieasured
b TBTC = tributfltia chloride. TBTf = tributyltia fluoride. TBTO = tributyltin oxide. TBTS - tributyltin sulfide Percent purity
is given in parentheses ibeo available
c Concentration of the tributyllin cation, not the chemical IT the concentrations were not measured and Ihe
published results «ere nol reported to be adjusted for purity, the published results iere multiplied by the purity il il
•as reported to be less than 95Z
-------
Table I (collided)
d Value not used ia determination of Species Mean Acute Value (see text)
* Value not used la determination of Species Mean Acute Value because data are available for a aore sensitive life
' The test organises core exposed to leachote from paaels coated »ilh onlifouling paint containing a tributyltin
polyeiar and cupraul a«lde. Concentrations of IBT >ere measured and the authors provided data to demonstrate the
similar toiicity of a pure TBT compound and the TBT froo the paint fornulalion
9 LC5Q or CCSO calculated or interpolated graphically based on the authors data
-------
Table 2 Chroeic Toiicity of Tritutv.lt i* te Azotic Aei
Specie* Ta»ta
Cladoc«raa. LC
Oaphnia nmana
fathead ninnoi, CIS
Pimephales promelas
Cbeaicol*
TBTO
(961)
TBTO
(961)
Hardeess
(•g/L as Linits
SPfCIES
51 S
SI 5
0 1-0 2
0 15-Q 45
Ckroiic Value
0 1414
U 2598
»efere»c«
Arooke el al I486
Brooke el al 1986
Hysid.
iconthaosis scul ola
LC
S»LTW«TIB SPCCICS
0 09-0 19
0 1308
Davidson el al )9B6e,b
" 1C = life-ejcle er partial lira-cycle. CIS = aarly life-stage
b TBTO = tribulyltin oiide Percent purity is givaa la poreplheses ib«n available
c Measured coecentraiioos of the tributyltin calion
d The test argooisas ware en posed to leachat* from panels caoted eith ontifauling paint containing a tnbulyltin
polyaer and typraus and* Concent rat ions of TBT .ere •ensured and Ibe avlkors provided data la denoostrale the
jiailar taxicity of a pure TBT compound and the TBT fro« the paint foraulalion
-------
Table 2 (cotliiued)
*cu>e-CI>ro«ic Botio
Harness
(•9/L as Acute Valee Chroeic Waive
Sveciea CoCO.) (ua/Ll
Cladeceran. 51 5 43
OoDhnlo aogno
Fathead •iaaoe. 51 5 26
Piaephales promelos
Uysid. - 0 61°
Acanlhoovsis sculnta
(ua/l) Ratio
0 1414 30-41
0 2598 10 Ul
0 1308 4 66'
0 Reported by Valkirs et al (I985a)
Ul
-------
I obi* J. Ranked Genus Heat Acute Values •ilk Species Mean Acute-Chronic Ratios
Ceeiis tteee. Species Heae Species Mean
Acute Heine Acute Value Acute-Cheat ic
Ro»ta (m/ll Species tinJO* Ratio6
seccits
B 10 2 Mosquito. 10 2
Cul«« sp
1 55 Channel catfish. 55
let ol urus punclot us
6 54 Annel id. 34
Lumbriculus van taotus
5 41 Clodoceron. * 1 iU 41
Doahnio ma an a
10
cr> 4 3 9 Rainboe trout. 39
Sol mo aairdner i
i J 7 Aaphipod. J 7
arus pseudol imnqeus
2 6 falkead mianon. 26 10 Ul
PimephaJes proinelos
0 5 Hydra. 0 5
-------
Table 1 (caatieued)
Genus Ueee Species Mean Species yean
Acete Velue Aeule Value Acute-Chronic
Bonk" (u«/U Species lua/ll* Ratio*
S/HIWATtB SPtCUS
18 204 4 European flal oyster. 204 4
Ostreo edulis
17 83 28 Shore crab. 81 28
HemiorgpMis midus
16 14 90 Uud crab, 14 90
PhiIhroponopeus horrisii
IS 21 16 yuaaicho], 21 16
fundulus helerocIilus
14 >I4 6U Anphipod. >14 60
Orchestia Irostiana
13 9 712 Shore crab. 9 712
Carttnus noenos
12 6 812 Polychaete. 6 812
Keanthes orenoceodentoto
II 2 115 Sheepshead minnoi. 2 115
Cwofinodon vorieaolus
ID 2 218 Blue oussel. 2 218
y»>ilus edulis
g 22 Copepod. 22
Curvlemoro aft i ni!»
-------
Table 3 (coatitued)
ro
CO
Gems Uea*
Acute Value
Ha nil a lua/il
B
I 911
745
I 460
I 365
I 204
<0 9732
Q 6326
0 61
Copepod,
Mitocro spinipes
American lobster.
Homorus omen conus
Chinook salmon.
Oncorhnnchus tsho»v1scho
Hard elan.
Mercenor10 mercenor10
Pacific oyster.
Crossostreo qiqos
Eastern oyster.
Crosses!reo viroi nico
Uysid.
Metomvsidopsis elongate
Copepod.
Acortio tonso
Mysid.,.
Aconthonvsis sculpto
Species yaae
Acute Valve
tue/ll*
I 911
I 460
I 365
557
0 9316
!>7. ol Hie i-.|lo-ud "'V •"'•••
-------
Table 3 (continued)
Fresh water
Final Acute Value = U 2972
Criterion Maximum Concentration = (0 2972 yjg/L) / 2 = 0 1486/ig/L
Final Acute-Chronic Ratio - II 24 (see text)
Final Chronic Value = (0 2972 jig/L) / 11 24 = 0 02644 Mg/l
Sail »oter
Final Acute Value = 0 5313 /ig/L
Criterion Maximum Concentration = (0 SJI3 /jg/L) / 2 = 0 2656 /jg/l
Final Acute-Chronic Ratio = II 24 (see text)
Final Chronic Value = (0 5313 pg/l) / 11 24 = 0 04727 ^g/L
Final Chronic Value = 0 010 jig/L (lowered to protect molluscs, see text)
-------
Totle 4 Toiicity of Tributyltin la Aquatic Plaels
LJ
c
Snecies
Alga,
Bum I ler ions is fill formis
Alga,
Klebsormidi urn mor inum
Alga.
Honodus subterraneus
Alga.
Raphi donemo lonoiseto
Alga.
Tnbonemo aeauale
Blue-green alga.
Osci I lolcna sp
Blue-gre«n alga.
Siinechoceccus leopol leasis
Green olga.
CMonvdoiionos dvsosmos
Green alga,
Chlarel In eaersoni i
Green alga,
Kirchner lei la contorlo
Hordeess
(.g/L .,)
l
1BTC
WC
IHC
TBIC
1BIC
1BTC
1BTC
1B1C
IBTC
IBIC
Duralioi CoDcentral i a*
(davsl Errecl («a/L)b
fBCSH»ATt» SPCCIES
14 No gro.th 1114
14 Ha gro.th 222 B
14 No gro.th 1.782 2
14 Ho gro.th 56 1
14 Ho gro.th 1114
14 Ho gro.th 222 B
14 Ho gro.th III 4
14 Ho groilb III 4
14 Ho groilh 445 5
14 Ho gro.th III 4
Deference
Bland
Bland
Bland
Bland
Bland
Bland
Bland
Blanck
Bland
Blanck
Blond
Bland
Blanck
Blanck
Blanck
Blanck
Bl and
flland
Blanck
Bin nd
1986.
el al
I9B6.
el al
ISB6,
et al
1986.
et al
1986,
el ol
I9B6.
et al
I 986,
el al
1986,
et al
1906.
et al
IOBG.
el ill
1984
I 96*4
1984
1984
1984
1984
1984
1984
1984
1984
-------
Table 4 (continued)
Hardness
(l/L as
Species Chemical
Green alga, TBTC
ktonoroptii di um pusi I lum
Green alga, TBTC
Scenedesmus obtusiusculus
Green alga, TBTC
Selenostrum capricornut um
Ovralioe
(dons!
14
14
14
Cancentralloa
Iffect (Ma/Llb
Mo grovth 1114
Mo grovth
Ma growth
445 5
1114
Reference
Blanck I9B6.
blonck el al 1984
Blunck 1986.
blani.k el al 1984
Blonck 1986.
Blanck el ol 1984
SPEC us
Diatom.
Skel elonema costatum
Diatom.
Skel et onema costal UP
Diatom.
Steletonema costal ui»
TBTO
TBfO 30C
(BiokUt Red)
TBTO 30*
(olkyl source)
5 Algistat ic
algicidol
14 IC5U
(dry cell
•eight)
14 K5U
(dry cell
•eight)
0 9712-17 52 Ihain I98i
>I7 52
>0 1216.
-------
Table 5. Bioaccuaulatio» of Tributylli* by Aquatic Organises
Solioity
Species Cheaicol0 («/l«)
Green olgo. TBTO
Ank i si rodesmus f olcolus
Concentration
IB Voter (ua/LI*
r»tSHW*TIH
5 2
4 7
2 1
1 5
Ourat JOB
(dais) Tissue
SPCCICS
7
14
21
28
Bcr i
_Bil!
300
253
448
467
Reference
Uaguire et al 1984
SOLTMTtH SPCCUS
Blue mussel
(spot).
U»tilus edulis
Pacific oyster.
Crossostrea Qiaos
Pacific oyster.
Crossostreo qiaos
Pacific oyster.
Crossostreo oiaos
Pacific oyster.
Crossostreo aiqos
Pacific oyster.
Crossostreo 01qos
Curopean
(lul oyiler.
0 .1 f eg edul i'.
TBTO
TBTO
TBTO
TBTO
mo
28 5-34 2
28-31 5
28-31 5
28 5-34 2
29-32
29-32
28-31 5
0 24 45 Soft 6.833°
ports
1 2IE 21 Soft I.B74e
ports
0 1460 21 Soft 6.U47"
ports
0 24 45 Salt 7.292e
parts
1 557 56 Soft 2.300
parts
0 1460 56 Soft II.4UO
parts
1 216 21 Soil 96lle
par 1 j
Tho i n and
Wuldack 1985.
Thain 1986
Vfaldock
el al 1983
Ufa Nock
et al 1983
Tha i n and
tfuldock 1985.
Tho in 1986
Wai Jock and
Thain 1983
Wuldock and
Ilio.n IU8J
W.ildutt
el ul I9t)i
-------
Table b (continued)
ui
ui
Special
European
Mat oyster.
Ostreo edul is
European
Hal oyster.
Obt reo edul i s
European
f lal oyster.
Ostreo edul is
European
Mot oyster.
Ostreo edul is
Salieity Coecealrat ioe Duration
Clerical* (a/kal le later l«ja/llk
-------
Table 6 Other Data ae Effects of Tributyltie ae Aquatic Orgaeisws
Special
Algae.
Natural assenblge
Bl ue-jreen alga,
Anabocna f Ips-oauae
Green alga.
Antistfodesntus falcotus
Green alga.
Scenedesaiis QiiaJn taudo
Clan (larva).
Corpic«la Muainea
Cl gdoceron.
Oaahnia mgqnq
Claooceran (<24 br),
Dap tin to moqna
Cladocarao ((24 hr).
Baphnio aaana
Cladaceron (adult).
Oopbnia poana
Rainbo* trout (yearling).
So Iroo aoi rdner i
Mardeess
(-9/1 «
Chemical" CaCOjl Durglio* tit eel
fBtSHMTCB SPCCItS
4 hr CCSO
(product ion)
4 hr CCSO
(reproducl ion)
4 hr USD
(product too)
(reproduction)
4 hr CCSD
(product ion)
TBIO - 24 br CCSO
TBTQ - 24 hr LC5Q
TBIC 20D 24 hr EC 50
(nobility)
IBTO 20U 24 hr CCSO
(mobility)
TBTC * A days Al tered
TBTO - 24 hr lf.50
40 hr
Concektral ion
-------
Table 6 (ci. . iaued)
CJ
01
Species
Roinboi trout.
Solan) aoirdnan
Roinboa trout (embryo. lar»o),
SoImo oairdneri
frog (embryo, larva).
Rono tempororia
Cheaicol"
TBTO
TBTC
TBTO
TBTf
TBTO
TBTf
Hardiess
(•9/L as Coeceatrat toe
CoCOjl Oyralio. tffeel l««Alb
24 hr CC50 30 8
(rheotoms)
94-102 110 days 201 reduction 0 IB
in groith
2JZ reduction 0 B9
in groilh. 6 61
mortal i ty
IOOZ mortality 4 46
5 days LC40 28 4
5 days LCSO 28 2
S days Loss of body 28 4
•ater
S days Loss of body 2B 2
•aler
Helereoce
Chi lamovi ten
and Kuhn 1977
Semen el al
I9BI
Lauglil i n and
Linden 1982
-------
Table 6 (continued)
Species
Natural nicrobial
populat i ons
Natural microbiol
popul at i ans
Green alga,
Ounal iel 1 a SB
Green alga.
Durtdl lella sp
Oialon.
PhaaodoctKliiin
Iritornulua
Diaton.
Steletoneao
costotua
Oiotoa.
Stel etonena
castatup
Salinity Caecentrat ion
Chemical" (a/to) Duration Cffect (u«/l|b
SmiMTtB SPCCUS
TBTC 2 and 17 1 hr Significant 4 454
decrease in
aelabol ism af
nutrient
substrates
TBTC 2 and 17 1 hr 501 89 07
{incubated aortal ity
10 days)
TITO - 72 hr Appro! CCSO 1 460
(groilh)
TBTO - 72 hr IOOZ 2 970
•ortal i ty
TBTO - 72 hr No effect 1 460-5 819
on gro»lb
TBTA 10 72 hr CCSO 0 J097
(population
groetfe)
TBTA JO 72 hr 1C 50 12 65
Heference
Jonas el
1984
Jonas el
1984
SaJ amr
Sal azar
S
-------
Table 6 (continued)
Spec i as
OlOlOD.
Steletonemo
cost o tun
Diatom,
Steletonemo
costalure
Diatom.
Steletonemo
costolum
0 1 a I on .
Stel el onema
costolum
Diatom.
Steletonema
costotun
Diatom.
Stel etonemo
cost plum
Diatom.
Iholoss losiro
psaudongno
D tot on.
Iholossiosiro
pseudonono
Solicit*
Ckeaicol0 I«A«)
1BTO 10
TBTO 30
1BTC 30
TBTC 30
IBTf 30
TBTf 30
TBTA 30
1BTO 30
Coaceolrat ion
Duralin* Eff.ct (iia/L)b
72 hr CCSO 0 3212
(populat ion
groilh)
72 hr LC50 13 82
72 hr CCSO 0 3207
(populat ion
grovlh)
72 hr LC50 IU 24
72 hr IC50 >0 2346.
(population <0 4693
groith)
72 hr LC50 1117
72 hr CCSO 1 101
(populat ion
grovlh)
72 hr CCSO 1 002
(populat ion
groilh)
Betercpce
Walbh el
1985
Wolbh et
1985
Walih et
1985
Wolbh el
I9BS
Wal^h et
1985
Walsh et
1985
Wulih et
1985
Walbh et
1985
al
al
al
al
al
al
al
ul
-------
Table 6 (continued)
00
Oinaflagel late.
Cvmnedioium
sol anJens
OogvheU (adult).
Hucel la InpiIlus
Vud snail (adult),
HassofiuS
ofasoletuS
61 ue mussel (spat),
Uvl11 us eJul is
Blue mussel (spat).
edulis
Blue mussel (larva),
eaulis
Blue nussel (juvenile).
adelis
Selieiti
Chemical0 («/ia)
TBTO
c
Duration
72 hr
120 days
Concaetral ion
meet fua/U*
IOOZ 1 460
nortal i ly
4IX Impose. 0 05
( super imposi t ion
Reference
Soloior 1985
Bryan el
1986
al
IBTO
28 5-J4 2
28 5-J4 2
TBTO
T&TO
31 J
days
of male anatomical
characteristics on
f eaaIes)
Impose*
Smith 1981
45 days
45 days
IS days
7 days
Significant Q 24
reduction in
growth, ae
aortal i ty
IOOX 26
atortaltl y
SIX nortal ity. 0 0973
raauced grovlti
Si^nificenl 0 3893
reduct i on
in growth
Itiain and
Wai dock 1985
Ihatn 1986
Thuin and
Waldact 1985
Ihain 1986
Beaumont and
Budd 1984
Slromgr en
and Bongard
19»?
-------
Table 6 (canticiued)
Chemical"
LJ
VO
Blue mussel
(2 5 to 4 I cm).
HvtiI us edulis
Blue mussel
(2 5 to 4 I cm).
UvtiI us edulis
Pacific oyster (spat),
Crassostreo qiqos
Pacific oyster (spat).
Crassestreo qiqas
Pacific oyster (spat),
Crossostrea aigas
Pacific oyster (spal),
Crossostreo qiqas
Pacific oyster (larva),
Crossostreo
PaciTic oyster (larva),
Crossostrea aioas
Paci fic oyster (larva),
Crossostreo qiqas
TBTO
TBTO
Salinity
U/tak
-
28 5-14 2
28 5-34 2
29-32
29-32
-
-
Ourat ion
66 days
66 days
45 days
45 days
56 days
56 days
30 days
113 days
Concent rat ion
[Cfect («q/L|b
LCSO 0 97
$1901 f icon! 0 31
decrease in
she! 1 gronth
401 mortal ity. U 24
reduced gro»lh
9QX 2 6
aortal ity
Ho gro.th 1 557
Reduced groith U I46G
IOOZ 2 0
aortal i ty
30 X mortality 0 2
and abnormal
development
Kef ercnce
Vail irs et al
l9Bb. 1987
Yalkirs et al
1985
1 hai n and
Wai dock 1985.
lhain 1986
Tha i n and
Waldack 1985
Wo 1 dock and
Thain 1983
Waldock and
Thain 1983
Al 11 eu et al
I98U
Al 2 1 eu et al
I9SU
TBTf
18-21
21 days Reduced number 0 02346
of normally
developed
larvae and
selling of spat
Spnnijboin Bionomics
I984u
-------
lable 6 (continued)
Sal ioi ty
Spec ins Chemical0 (
-------
Table 6. (coititued)
Sp«eias Ckeaical
European (lot oyster (spat). c
Ostreo edulis
European flat oyster (spat). c
Ostreo edul is
[uropean flat oyster (adult). c
Ostreo edul i s
[uropean flat oyster (adult), c
Ostreo edul is
European (lot oyster (adult). c
Ostreo edul is
Hard don (post larva). TBTC
Mercenorio aerceoario (95X)
Hard clam (post larva). TBIC
yereenorio aercenaria (951)
Soli.ily Concentration
(a/kak Ourolioa Effect (|iq/L)
28 5-34 2 45 days Decreased 0 2392
groitb
28 5-14 2 45 days 70X mortality 2 6
28-34 75 doys Complete 0 24
inbibi 1 ion
of larval
product ion
28-34 75 days Retardation 0 24
of sex change
from male to
f ena 1 e
28-34 75 days Prevented 2 6
gonadol
development
96 hr Inhibited 0 OOU7J30
siiMing
behavior
96 hr Reduced 0 OU2922
nuaber of
aninals
developing
a foot
Refereece
Ihuin and
Wul dock 1985.
Ihain 1986
Thain and
Wai dock I98S.
Thain 1986
Thain 1986
Ihain 1986
Thain 1986
Becerra-
Huencho 1984
Becerro-
Huencho 1984
Hard clam (embryo, lorxa).
Uercenaria mercenor10
TBIO
14 days Reduced
-------
Table 6 (cont i noed)
S fee I es
Hard clan ( larva) ,
Uerceiiarja merceneri a
Hard clan (post larva),
Hefcenorio mercenorio
Hard clan ( larva) ,
Merceoor i a mercenan a
Clam (adult).
Protottiaco slam no
Copepad,
[urvtemoro otl mi s
Copepad.
[urvtenora offinis
Copepad.
Acort IP tonsa
Aaphipod (larva, juvenile),
Cqnaqrus oceacus
Amphipod (larva, juvenile).
Cammarus eceanus
Aaphipod (larva, juvenile),
Gommorus eceonus
Amphipod (larva, juvenile]
r*iminflr us nrpanus
Salinilf
Cheaicol" .2 92U
II days Reduced survival 0 088
of aeonates and
adults
1} days Reduced survival 0 224
of aeanates
144 hr CC50 0 3891
B ik (DOS mortality 2 920
6 it IOOZ mortality 2 816
8 ik Reduced 0 2920
survi val
and f,ro*th
fl «k Reduced U 2UIC
lurv i val and
Reference
Laugh! to et al 198?
Laughlin et al 1987
Roberts. Manuscript
Salazar and
Sal ajar, Uanubcr i pi
Hal 1 el al 1987
Hall et al 1987
U'ren 1985
laugal in et al
I984b
laugh 1 i n el al
I984b
(.ought in et al
I984b
1 uuylil i n et u|
1 'JtiAb
i ncreo^eJ giu«th
-------
Table 6. (continued)
Species
Amphipod (adult).
Orchest i e trosfc iano
Amphipod (adult).
Orchest 10 trosfc long
Crass shrimp.
Pol oemoneles puqio
Mud crab (larva).
Rhi Ihropanopeus horrisi i
Hud crab ( larva) .
Rhi Ihropanopeus horrisi i
Hud crab (larva).
Rhi Ihropanopeus horrisi i
Hud crab (larva).
Rhi Ihropanopeus horrisi i
Hud crab,
Rhi Ihropanopeus horrisi i
Hud crab.
Rhi throponopeus herrisi i
Uud crab.
Rhi I hropanopeus horr i si i
Chemical"
TBTO
TBTf
TBTO
(95X)
TBTO
TBTS
TBTO
TBTS
TBTO
TBTO
TBIO
Salinity
la/kal
3D
30
99-11 2
15
15
15
15
15
15
15
Ourat ion
9 days
9 days
2U mm
15 days
IS days
15 days
15 days
6 days
6 days
6 days
Concentration
Effect (tia/Llb
Appro* BUZ 9 732
mortal i ly
Appro* 901 9 732
mortal i ty
No avoidance 30
Reduced 14 60
developmental
role and groith
Reduced 18 95
developmental
rate and groit-h
63X Mortality >24 33
74X Mortality 28 43
BCf=24 5 937
for carapace
BCf=6 5 937
for hepoto-
paacreas
BCf = 0 6 5 937
for levies
Reference
Laughl in et al
1982
loughl in et al
1982
Pinkney el al 1985
Laughl in et al
1983
Laughl in el al
1983
Laughl in et al
1983
Laughl in et al
1983
[vans and
Laughlin 1984
(vans and
Laughlin 1984
1 vunb and
ItiuuJiliN 1984
-------
Table 6. (coatiauad)
Species Cheaical*
Uud crab. TBTO
Rhi Ihrooanopeus horrisi i
Uud crab. TBIO
Rhi thr oconooeus horr is i I
Tiddler crab. TBTO
Uca pug i lotor
Atlantic aenhaden (juvenile). TBIO
BrevooHio tvronnus
Chinook salmon (adult). TBTO
Oncorhvnchus tsho»vtscha
Chinook salmon (adult). TBTO
Oncorhvnchus lsha»v tscho
Chinook salmon (adult). TBTO
Oncorhvnchus tshawvtstho
Uunaichag. IBTO
f undulus heterocl i tus (951)
Col i fornia gruoian c
( gamete through eabryo).
leuresthes tenuis
Col i fornia gruni on c
i n niHA 1 A ft hr n ii n h £mhr u n 1
Salinity Concentration
ia/ka) Duration tlfect Iua/Llb
15 6 days BCF=4I . 5 937
Tor gi 1 1
t issue
15 6 days BCf=l 5 for 5 937
chelae muse le
25 i24 days Retarded Imp 05
regeneration and
moll ing
9-11 - Avoidance 5 437
28 96 hr BCr=4300 1 49
for liver
28 96 hr BCr>)300 1 49
for brain
21 96 br BCf=200 1 49
lor auiscle
99-11 2 20 am Avoidance 3 7
10 days Significantly 0 14-1 72
enhanced
gravid and
hatching success
111 days 501 redact ion 74
in hatchi nq
Reference;
[vans and
Laugblin 1984
[vans and
Laughlin 1984
Weis et al 1987
Hall et al
1984
Short and Throier
I986a. c
Short and Thro>er
I986a.c
Short and Throier
I986a.c
Pinlcney el al 1985
N««tan et al
1985
Neilon et ul
I'JaS
I euf ea tliea lenui s
-------
Table G (cantitu«d)
Selieity
Coecentratroe
California gruniaa (enbryo).
leuresthes lenuis
California grunion (larva).
Ieureslhes lenui s
Striped bass (juvenile).
Horone Sonet i I is
Speckled sanddab (adult).
Chithorichthys stigneous
Cboicol'
(a/ til Duratioe I If eel
10 days Ho adverse
effect on
hatching
success or
groith
7 days Survival
increased as
concentral i on
increased
loa/LT
Q 14-1 72
U 14-1 72
TBTO
(951)
WO
9-11
96 br
Avoidance
USD
24 9
IB 5
Hef erence
Neiton et al
I 985
Meilan el ol
1985
Noll et al
I9S4
Solozor and Soloior.
Manuscript
" TBU = tributyltin acetate. TflIC = Inbutyltin chloride. TBIf - IributvlliD fluoride. TBTO = Inbutvltin amde.
= tribulyltin sulfide Percent penly is givto in porcntlteiies idea
b Cancenlral ion of the tributyltia cation, not the cbemical If the concentral ions eere not aeosured and the published results »ere not
reported to be adjusted for purity, the published results eere Multiplied by the purity if it »os reported to be less, than 9SZ
c The lest organises eere exposed lo leachale Iron) panels coated eitb antifauliog paint containing tribulyltin
The test organisms were exposed to leachale Iron panels coaled lilh anlifouling paint coataining a Inbutyltin polymer
and cuprous onde Concentrations of TBT «ere measured and th« authors provided data to demonstrate the similar laxicily of a
pure TBT coopound and the IBT from the paint formulation
-------
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-------
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