Ambient Aquatic Life Water Quality Advisories for Tributyltin


                                               600R87053
                                                      9/14/87
AMBIENT AQUATIC LIFE  WATER  QUALITY ADVISORIES FOR

                   TRIBUTYLTIN
      U.S. ENVIRONMENTAL PROTECTION AGENCY
       OFFICE OF RESEARCH AND DEVELOPMENT
       ENVIRONMENTAL RESEARCH LABORATORIES
                DULUTH,  MINNESOTA
           NARRAGANSETT, RHODE ISLAND

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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.
                                       11

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                                   FOREWORD
     The Criteria and Standards Division of the Office of Water Regulations
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 quickly,
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. Notzon, Director
                                       Criteria and Standards Division
                                      111

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                           ACKNOWLEDGMENTS
Loren J.  Larson, freshwater contributor
    University of Wisconsin-Superior, Superior,  WI

R. Scott Carr, saltwater contributor
Jeffrey L.  Hyland,  saltwater contributor
    Battelle Ocean Sciences, Duxbury, MA

David J.  Hansen, saltwater coordinator
    Environmental Research Laboratory, Narragansett,  RI

Charles E.  Stephan,  document coordinator
    Environmental Research Laboratory, Duluth, MN
                                  IV

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                             CONTENTS
                                                               Page
Foreword	    i i i
Acknowledgments 	     iv
Tables	     vi

Introduction  	      1
                                                        •
Background Information  	      3
Acute Toxicity to Aquatic Animals 	      6
Chronic Toxicity to Aquatic Animals 	      9
Toxicity to Aquatic Plants  	     11
Bioaccumulation 	     12
Other Data	     12
Unused Data	     15
Summary	•> .  .  .     17
Aquatic Life Advisories 	     18

References	     48

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                                    TABLES




                                                                     Page




1.   Acute Toxicity of Tributyltin to Aquatic Animals 	     20




2.   Chronic Toxicity of Tributyltin to Aquatic Animals 	     26




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




      Ratios	28




4.   Toxicity of Tributyltin to Aquatic Plants  	     32




5.   Bioaccumulation of Tributyltin by Aquatic Organisms  ......     34




6.   Other Data on Effects of Tributyltin on Aquatic Organisms  .  .     36
                                       VI

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INTRODUCTION

     The  Water Quality Advisory Document has been  developed  to
provide technical guidance and the best available scientific data
on the adverse effects of chemicals in surface waters.   Advisory
concentrations represent levels of contaminants in surface waters
and  drinking water at which adverse effects to human health  and
aquatic life would not be anticipated to occur.  An advisory  may
be issued for any chemical when there is need for information but
where  insufficient  data exist to calculate a  national  ambient
water quality criterion.

     An  ambient  water quality advisory  concentration  for  the
protection of aquatic life will be derived from aquatic  toxicity
data   in  accordance  with  the  procedures  describes  in   the
Guidelines for Deriving Aquatic Life Advisory Concentrations.

     An  ambient  water quality advisory  concentration  for  the
protection  of  human  health  may be derived from  a  number  of
sources:   The Office of Drinking Water Health Advisories;  Agency
verified  Reference Dose (RfD) values; Office of  Pesticides  and
Toxic Substances risk estimates; risk estimates originating  from
open  literature  or  other sources which will be  cited  in  the
support document.

     Prior to application of an advisory concentration,  the  user
should  carefully review the supportive data within the  advisory
document  and develop an understanding of the derivation  of  the
advisory recommendation.

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Background Information




    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^HgJgSn^.  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).




    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 most




toxic organotin 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




                                       3

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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



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 time between repainting from less than 5 years to 5 to




7 years.  Release of TBT to water would occur 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 (Corbin 1976).



The solubility of tributyltin oxide in water was  reported to be 750 Mg/L at



a pH of 6.6 and 31,000 ng/L at a pH of 8.1 (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).




    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




                                       4

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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 monobuty1tin,  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. Maguire et al. (1984) reported that a 28-day culture of TBT with



the green alga, Anki strodesmus 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 ^g/kg 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)




                                       5

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 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.  An understanding of the "Guidelines  for Deriving



 Numerical National Water Quality Criteria for the Protection of Aquatic




 Organisms and Their  Uses"  (Stephan et al. 1985), hereinafter referred to as



 the Guidelines,  and  the response to public comment (U.S. EPA 1985a) is



 necessary 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  February 1986; some more recent  information was



 i ncluded.








 Acute 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 /ig/L for a mosquito, Culex sp.  The 96-hr LC50 of



 227.4 M«A reported  by Foster (1981) 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




                                       6

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Values (Table 3) were calculated as geometric means 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, Cutex.   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 ng/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.



    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 98-hr LC50 of 0.01466 ng/L reported by Becerra-Huencho



(1984) for post larvae of the hard clam,  Mercenaria mercenaria.  also known as




the 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 ng/L for embryos



and 1.65 ng/L for larvae of the hard clam.  Laughlin et al. (1987) 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 ng/L.  They found that post



larvae were more resistant than larvae; concentrations <:• 7.5 ng/L did not



reduce survival after 25 days, but 10 ng/L caused 100% mortality.  Results



from these tests, in which concentrations of TBT were measured,  differ




markedly from the LC50 of 0.01466 jug/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

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post-larval clams, mussels, and oysters indicate that acutely lethal




concentrations are in the range of 0.6 to 4.0 ng/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 Mg/L for juveniles of the mysid,  Acanthomysis  sculpta (Davidson



et al.  1986a,b) to 282.2 ng/L for adult Pacific oysters,  Crassostrea gi gas



(Thain 1983).   The 96-hr LCSOs for three saltwater fish species range from



1.460 MgA f°r juvenile chinook salmon, Oncorhynchus tshawytscha (Short  and



Thrower 1986b) to 23.36 ng/L for adult mummichogs, Fundulus heteroclitus



(EG&G Bionomics 1976).




    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




282.2 /ug/L (Thain 1983).   In renewal tests, the 96-hr LC50s for larval and




adult blue mussels, Mytilus edulis. were 2.238 and 36.98 MK/L, respectively




(Thain 1983).   Juveniles of the crustaceans Acanthomysi s sculpta and




Metamvsidopsi s 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 ng/L for Acanthomysis to 204.4 ng/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 crustraceans, and two species of fish.  The saltwater Final



Acute Value for TBT was calculated to be 0.5313 /ig/L (Table 3), which is




lower than the lowest saltwater Species Mean Acute Value.

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Chronic Toxicitv 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)




reported that the survival of Daphnia magna was 40% at a TBT concentration of




0.5 /ug/L, and 100% at 0.2 ng/L.  The mean number of young was reduced



30% by 0.2 ng/L, and was reduced 6% by 0.1 ng/L.  The chronic value for



Daphnia magna was calculated to be 0.1414 p.g/L, and the acute-chronic ratio




was 30.41.



    In an early life-stage test with the fathead minnow, Pimephales promelas,




all fish exposed to 2.20 pg/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




higher than in the controls at 0.45 jug/L and lower concentrations.  The



mean weight of the surviving fish was reduced 4% at 0.08 Mg/L. 9^ at




0.15 Mg/L. 26% at 0.45 ng/L, and 48% at 0.92 /ig/L.  The mean biomass




at the end of the test was higher at 0.08 and 0.15 MgA than in the



controls, but was reduced by 13 and 52% at TBT concentrations of 0.45 and




0.92 pg/L, respectively.  Because the reductions in weight were small and




the mean biomass increased at 0.08 and 0.15 ng/L, the chronic limits are




0.15 and 0.45 ng/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,



Acanthomysis sculota (Davidson et al. 1986a,b) and the sheepshead minnow,




Cvprinodon varietatus (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 jug/L was 50% of the number released in the




control treatment,  whereas the number released at 0.09 jug/L was higher than




in the control  treatment.   The data concerning the effects of TBT on survival



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and growth are not easy to interpret.   At concentrations from 0.08 to




0.27 jug/L, survival and weight were sometimes equal  to or better than in



the control treatment,  but at concentrations of 0.38 /ug/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 Cyprinodon



variegatus (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




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



Pimephales promelas.  and 4.664 for Acanthomvsi s sculpta.  Division of the




freshwater and saltwater Final Acute Values by 11.24 results in freshwater and



saltwater Final Chronic Values of 0.02644 and 0.04727 ng/L, respectively



(Table 3).  Both of these Final Chronic Values are below the experimentally



determined chronic values.



    Unacceptable effects on commercially important saltwater molluscs occurred



at TBT concentrations less than 0.04727 /ig/L (Table  6).  Growth or



development of the Pacific oyster, European flat oyster, and hard clam was



reduced at 0.023;  0.019, and 0.025 MgA, respectively.  A TBT concentration




of 0.047 jug/L was  lethal to larval C.  gjgas.  Because adverse effects on




important saltwater species have been documented to  occur at concentrations as
                                       10

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low as 0.019 MS/L, the saltwater Final Chronic Value is lowered to



0.010 Mg/L to adequately protect these important species.
Toxicitv 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 jug/L.




No data are available on the effects of TBT on freshwater vascular plants.



    Toxicity tests on TBT have been conducted with five specie.s of saltwater




phytoplankton including the green alga, Puna 1 i e 1 1 a sp. ; the diatoms,



Phaeodactvlum tricornutum.  Skeletonema costatum.  and Thai lassiosi ra




pseudonana:  and the dinof lagel late , Gvmnodinium splendens (Tables 4 and 6).




The 14-day EC50 of 0.06228 jUg/L for S.  costatum (EG&G Bionomics 1981c) was




the lowest value reported,  but Thain (1983) reported that a measured




concentration of 0.9732 jug/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 jug/I (Table 6).   Lethal concentrations were  generally more than an




order-of-magnitude greater than ECSOs and ranged from 1.460 to 13.82 ng/L.



Identical tests conducted on tributyltin acetate,  tributyltin chloride,



tributyltin fluoride,  and tributyltin oxide with S..  costatum resulted in EC50s



from 0.2346 to 0.4693 ng/L and LCSOs from 10.24 to 13.82 ng/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.  However, the available data indicate that freshwater




and saltwater plants will be protected by concentrations that adequately




protect freshwater and saltwater animals.




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Bi oaccumulati on



    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 Waldock (1985) reported a BCF of 6,833 for the




soft parts of blue mussel spat exposed to 0.24 ^g/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 ng/L for 56




days (Waldock and Thain 1983).  A BCF of 6,047 was observed for the soft parts




of the Pacific oyster exposed to 0.1460 jug/L for 21 days (Waldock et  al.




1983).  The lowest steady-state BCF reported for a bivalve was 192.3  for the




soft parts of the European flat oyster, Ostrea eduli s. exposed to a TBT



concentration of 2.62 /ug/L for 45 days (Thain 1988; 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.  Foster (1981) reported a 24-hr EC50 of



1,990  ng/L for larvae of the clam, 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 fig/L 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 ng/L with rainbow trout, Salmo gai rdneri (Alabaster




                                       12

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1969).   Seinen et al.  (1981) exposed rainbow trout to 0.18 ng/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 superimposition




of male characteristics on female stenoglossan gastropods.  This phenomenon,



termed "imposes," can result in females with a penis, a duct leading to a vas



deferens, and the convolution of the normally straight oviduct (Smith 1981).




Exposure of N. 1api1lus to 0.05 ^g/L in a laboratory for f our ^months



produced a 41% incidence of impose* (Bryan et al.  1986).  Laboratory tests




with N. obsoletus and two TBT formulations also resulted in imposex but




exposure conditions were not stated (Smith 1981).   TBT has been linked to



imposex in field populations of Nucella lapillus.  Nassarius obsoletus.




Nassarius reticulatus. and Ocenebra erinacea (Bryan et al. 1988; Durchon 1982;




Smith 1981).  Imposex has been associated with reduced reproductive capacity




and altered density and population structure in field populations of N.




lapillus (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  ng/L



might be affected (Bryan et al. 1986).




    Reproductive  abnormalities have also been observed in the European flat



oyster  (Thain 1988).  After exposure for 75 days to a TBT concentration of



0.24 Mg/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 jug/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.




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Mortality of larval blue mussels, Mvtilus edulis.  exposed to 0.0973




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 pg/L (Stromgren and Bongard 1987;  Valkirs et al. 1985a).   The



66-day LC50 for 2.5 to 4.1 cm blue mussels was 0.97 ng/L (Valkirs et




al.1985a,1987).   Growth of hard clams from fertilization to metamorphosis was




reduced by 0.025 ng/L (Laughlin et al. 1987).   The number of larvae of  the



Pacific oyster,  Crassostrea gjgas. that developed and the number of spat that




set were reduced in 21-day exposures to 0.02346 ng/L (Springbarn Bionomics




1984a).  Alzieu et al. (1980) reported 30% mortality and abnormal shell




thickening among Pacific oyster larvae exposed to 0.2 /ig/L for 113  days.




Abnormal development was also observed in exposures of embryos for  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 ^g/L for 56 days.  Abnormal



shell development was observed in an exposure  to 0.77 jug/L that began with




embryos of the eastern oyster,  Crassostrea vi rginica. 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 >,OA ng/L



(Henderson 1986; Valkirs et al. 1985a).   Thain and Waldock (1985) observed a



significant reduction in growth of small spat  of the European flat  oyster,



Ostrea edulis. exposed for 20 days to a TBT concentration of 0.01946 Mg/L.



Growth of larger spat was marginally reduced by 0.2392 pg/L (Thain  1986;



Thain and Waldock 1985).




    Long-term exposures have been conducted with a number of saltwater




crustacean species.  Davidson et al. (1986a,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.




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Survival of larval amphipods, Gammarus oceanicus.  was significantly reduced




after eight weeks of exposure to TBT concentrations .> 0.2816 ng/L (Laughlin




et al. 1984b).  Developmental rates and growth of  larval mud crabs,



Rhi throoanopeus harri si i.  were reduced by a 15-day exposure to 2.




14.60 Mg/L-  B- harri si i  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 tenui s.  for ten




days to 74 MgA caused a 50% reduction in hatching success (Newton et al.




1985).  At TBT concentrations between 0.14 and 1.72 Mg/L,  growth, hatching



success, and survival were significantly enhanced.  Juvenile Atlantic



menhaden, Brevoortia tvrannus. avoided a TBT concentration of 5.437 /ug/L




and juvenile striped bass, Morone saxatilis. avoided 24.9 jig/L (Hall et  al.



1984).  BCFs were 4,300 for  liver, 1,300 for brain, and 200 for muscle tissue




of chinook salmon, Oncorhvnchus tshawytscha. exposed to 1.490 ng/L for 96



hours (Short and Thrower 1986a,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. 1964,1966a,b; de Sousa and Paulini



1970; Frick and DeJimenez  1964; Hopf and Muller 1962; Nishuichi and Yoshida




1972; Ritchie et al. 1964; Seiffer and Schoof 1967; Shiff 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




                                       15

-------
(1986),  Good et al.  (1980), Guard et al.  (1982),  Hall  and Pinkney (1985),




Hodge et al. (1979), International Joint  Commission (1976),  Jensen (1977),




Kimbrough (1978),  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 (1975,1985b),  U.S.  Navy (1984),  Valkirs et al.  (1985a),  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



Buzinova 1982;  de la Court 1980;  Deschiens 1968;  Filenko and  Isakova 1980;



Holwerda and Herwig 1986; Kolosova et al. 1980; Laughlin 1983;  Lee 1985;  EG&G



Bionomics 1981b;  Nosov and Kolosova 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 et 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 LC50.



    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; Salazar




and Salazar 1985a,b; 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.
                                       16

-------
    Data were not used when the test organisms were infested with tapeworms




(e.g., Hnath 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. 1982).   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 and French, Manuscript; Laughlin et al.




1986b).








Summary




    The acute toxicity values for eight freshwater animal species range from




0.5 jug/L for a hydra to 10.2 ng/L for a mosquito.  Chronic toxicity




tests have been conducted with two freshwater animals.  Reproduction of




Daohnia magna 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 yug/L.  but not by 0.15 ng/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 jug/L for the mysid,  Acanthomvsi s sculota. to 204.4 ng/L for adult




European flat oysters,  Ostrea edulis.  Acute values for the eleven 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




                                       17

-------
mysid,  Acanthomvsis sculpta.   The chronic value for A.  sculpta was




0.1308 M6/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 gjgas.  Imposex, which is the superimposition



of male characteristics on female stenoglossan gastropods, occurred among




Nucella lapi1lus exposed to 0.05 MgA in the laboratory and might occur in



field-exposed snails at 0.0024 ng/L.  For some species of snai.ls imposex




has been associated with reduced reproductive potential and population



density, particularly in the vicinity of marinas.  Growth or development was




reduced at 0.023 ng/L for Crassostrea gigas. 0.019 pg/L for Ostrea




eduli s.  and 0.025 MgA for Mercenaria mercenaria.  A TBT concentration of




0.047 pg/L was lethal to larval £.  gi gas.








Aquatic Life Advisories




    If the measured or estimated ambient concentration of tributyltin (TBT)



exceeds 0.028 ng/L in fresh water or 0.010 /ug/L in salt water, the



discharger, after consultation with an appropriate regulatory agency, should



evaluate the available exposure and effect data and complete one or more of



the following options within a reasonable period of time:



    a.   Obtain additional measurements of the ambient concentration.



    b.   Improve the estimate of the ambient concentration.



    c.   Obtain additional laboratory and/or field data on the effects of




        TBT on aquatic organisms and their uses so that a revised, and




        usually higher, aquatic life advisory concentration or a water




        quality criterion can be derived.
                                       18

-------
    d.  Conduct appropriate toxicity tests on the effluent.




    e.  Reduce the ambient concentration of TBT to an acceptable level.



After a reasonable period of time, an appropriate regulatory agency should




evaluate all available pertinent data concerning the ambient concentration and



the effects of TBT on aquatic organisms and their uses to determine whether it



is appropriate to take any action, such as modifying the discharge permit.



The analytical method used should distinguish TBT from inorganic tin and from



other organotin compounds (Laughlin et al. 1986a; Lee 1986; Maguire et al.



1984; Mathias et al.  1986; Valkirs et al.  1985b).
                                      19

-------
                                  Table I.   Acute Toxicity  of  Tributyltin  to Aquatic A»i*als

Spec i es yethod*
Hydro, S. if
Hydro sp.
Annelid (9 mg). F, U
Lumbr i cul us vorieqotus
Cladoceran, S. U
Dophni o moqno
Cladoceran (adult), S, U
Dophni o mo a no
O Cladoceran (<24 hr), F, U
Daphnio inogna
Amphipod, F, U
GomMorus pseudol imnoeus
Mosquito ( larva) , S, U
Cul ex sp.
Rainbow trout (juvenile), F, U
So into oo i rdner i
Fathead minnow (juvenile), F, U
Pinepholes promelos
Channel catfish F, U
(juveni le) ,
Ictol urus punct at us
Hardness LC50 Species yea*
(•g/L es or EC50 Acute Velne
th».irnlk C«CO,j_ (H^/1-)0 iutll]
FRESHWATER SPECIES
TBTO 51 0 0.5 05
(96X)
TBTO 51.8 54 54
(96X)
TBTO - 66.3d

TBTC - 5.26

TBTO 51.5 4.3 4.3
(96X)
TBTO 51.8 37 37
(96X)
TBTO 51.5 10.2 10.2
(96X)
TBTO 50.6 3.9 3.9
(961)
TBTO 51.5 2.6 ' 26
(96X)
TBTO 51.8 5.5 5.5
(96X)

Bluegi I I ,
Lepomi s  mocrocli i rus
S,  U
                                          TBTO
                                                                           227.4"
                                                                                                                 Reference
                                                                                                                  Brooke  et al.  1986
                                                                                                                  Brooke  et al.  1986
                                                                                                                  Foster  1981
                                                                                                                  Ueador  1986
                                                                                                                  Brooke  et  ol   1986
                                                                                                                  Brooke et  ol   1986
                                                                                                                  Brooke et  al   1986
                                                                                                                  Brooke et  ol   1986
                                                                                                                  Brooke et  al   1986
                                                                                                                  Brooke et  al   1986
                                                                                       Foster 1981

-------
           Table I.  (continued)
Spec i es
                                      Method"      Cfcemicel'
K>
Polychoete (juvenile), S, U
Neonthes arenaceodentoto
Polychoete (adult). S, U
Neonthes arenaceodeotata
Blue Mussel jlorvc), 8, -
Mvtilus edulis
Blue mussel (adult) , R, -
Mvt i 1 us edul is
Blue mussel (adult), S, U
Mvt i 1 us edul is
Pacific oyster (larva), R, -
Crossostrea ai gas
Pacific oyster (adult) , R, -
Crossostreo qiqos
Eastern oyster (embryo), S, U
Crassostrea virainica
Eastern oyster (embryo), R, U
Crassostreo virainica
T8TO
TITO
TITO
TITO
TITO
TBTO
TBTO
TBTO
(95X)
TBTC
          Eastern  oyster  (embryo),    R,  U
          Crossostreo  vi rqi ni ca
TBTC
Sal i«ity
(«/ka)
SALTVATER SPECIES
33-34
33-34
-
-
33-34
-
-
22
18-22
18-22
LCS
or E
luot
6.
21.
2.
36.
34
1 .
282.
0.
1.
0.
iO Species Mean
CSO Acute V«lve
L)e <«o/U
812
41* 6.812
238
98*
06* 2.238
557
2* 1.557
8759
30
71
                                                                        Reference
                                                                                                                             Solazor and  Solazar,
                                                                                                                             Manuscript

                                                                                                                             Solazar and  Solazar,
                                                                                                                             Manuscript

                                                                                                                             Thain  1983
                                                                                                                             Thain  1983
                                                                                                                             Salazar  and  Salazar,
                                                                                                                             Manuscri pt

                                                                                                                             Thain  1983
                                                                                                                  Thain 1983


                                                                                                                  EGtC Bionomics
                                                                                                                  1977

                                                                                                                  Roberts,  Manuscript


                                                                                                                  Roberts,  Manuscript

-------
Table I. (continued)
Species
Eastern oyster
Crossostreo virainico
European flat oyster
(adult),
Ostrea edul is
Hard clam
(post larva).
Mercenario mercenor I a
Hord clam (embryo),
Uercenori o mercenor I a
N)
10 Hard clam (larva).
Uercenori o mercenori a
Copepod ( juveni le) ,
Eurvtemoro of finis
Copepod (adult),
Acort la tonso
Copepod (adul t ) ,
Ni tocro spi ni pes
Copepod (adult),
Ni tocro spi ni pes
Mysi d ( j uveni le) ,
Acanthomvs i s scul pto
Sal i ni ty
Method41 Cke.icelb 
-------
          Table I.  (continued)
N)
Salinity
Species Method* Ckeaicel" (a/kq)
Mysid (adult). F. U f
Acont homysi s sculpta
Mysid (juvenile), S. U TBTO 33-34
Met flaws idopsis elongate.
Mysid (subodult). S, U TBTO 33-34
Metomvsidopsis elonqoto
Mysid (adult). S. U TBTO 33-34
Metomvs idopsis elonqota
Mysid (adult). S, U TBTO 33-34
Metamys idopsis elonqoto
Amphipod (adult), R. M TBTO 30
Orchest io troski ono
Amphipod (adult), R, M TBTF 30
Orchestia traskiano
American lobster (larva), R, U TBTO 32
Homo r us timer i conus
Shore crab (larva), R, - TBTO
Care i nus moenos
Mud crab (larva), R. U TBTS 15
Rhi throponopeus horrisi i
LC50 Species M««i
or CCSO Acute Melee
<«o/Ue (ua/L)
1.68* 0.61
<0.9732
I.9468
6.812*
2.433* <0 9732
>I4.609
> 14 08s >I4 60
I.7459 1 745
9.732 9.732
•
34. 909
Ref ere«ce
Valkirs et al . I985a
Salazar and Salazar,
Manuscript
Salazar and Salazar,
Manuscri pt
Salazar and Salazar,
Manuscript
Salazar and Salazar,
Manuscri pt
Laughl in et al 1982
Laughl in et al 1982
Laughl in and French I960
Thain 1983
Loughl in et al 1983
Mud crab (larva) ,
Rhi throponopeus horr i si i
                                    R, U
TBTO
                 15
>24.39
34.90
Laughlin et  al   1983
-------
Table I. (ce*tiiM«4)
Sp«ci«*                    yethod"      C»e«icalb

Shore crab (larva).        R. U           TBTO
Hemiqropsus nudus

Sheepsheod minnow          S, U           TBTO
(juvenile),
Cypri nodon vori eqatus

Sheepshead ninnot          S, U           TITO
(juvanile),
Cypr i nodon vori eaotus

Sheepshead minnow          S, U           TBTO
(j uvenile),
Cypri nodon vori eqatus

Sbeepsheod ainnoi          F, U           TBTO
(33-49 mm).
Cyprinodon vorieqotus

Uumaichog (adult),         S. U           TBTO
Cundulus heteroclitus                     (95X)
                Seli*itf
                 (a/ta)

                 32
                                                                             LC50
                                                                            or  EC50
                               Species yea*
                               Ac«te  Vel«e
Chinook salmon (juvenile),  S,
Oncorhvnchus tsho»vtscha
TBTO
                 20
                 20
                28-32
                 25
28
                  83 289
                                   16.54
                  16.54
                  12.65
                   2 3I5«
                  23 36
I  460
              83 28
               2.315
              23.36
                                  I .460
Reference

Laughlin and French I960


CGiG Bionomics 1979



EGIG Bionomics 1979



EGiG Bionomics 1979



EGtG Bionomics I98ld



EGIG Bionomics 1976


Short and Thrower 19866
  S = static;  R = reneial;   F  =  flow-through,   U =  measured;   U =  unmeasured.

  TBTC = tributyltin chloride;  TBTF  =  tributyltin fluoride;  TBTO =  tributyltin  oxide;  TBTS  =  tributyltin sulfide   Percent purity
  is given in parentheses vhen  available.

  Concentration of the tributyltin  cation,  not  the chemical.   If the  concentrations  nere  not  measured and the
  published results »ere not  reported  to  be adjusted for  purity, the  published  results  «ere multiplied by the purity if it
  •as reported to be less than  957
-------
         Table  I .  (cont inued)


            Value  not  used in determination  of  Species  Uean  Acute  Value  (see  text).

            Value  not  used in deter*!not ion  of  Species  Mean  Acute  Value  because data are available for a more sensitive life stage

            The  test  organisms  were exposed  to  leochote from ponels  coated  >ith ontifouting paint containing a tributyltin
            polymer  and  cuprous oxide.   Concentrations  of  TIT  were measured and Davidson et al. (I986a) demonstrated that  TBT
            in the  leachote had the s«*«  toxicity  as  TBT alone.

         '  LC5Q or  CC50 calculated or  interpolated graphically  based  on the  authors' data.
IS)
-------
                                             Table 2.   Chronic  Toxicity  of  Tributyltin  to Aquatic Animals
                Cladoceran,
                Oophni o moqno

                Fathead rainnc*,
                Pimepholes promelos
                                          Test'
LC
ELS
              Chemical'
TBTO
(96Z)

TBTO
(961)
         Hardness
         (•9/L «
          CaCOjl

FRESHWATER  SPECIES

            51.5


            51 5
                                                                                            Limits
0.1-0.2
0.15-0.45
                                                              Chronic  Value
                                                                  0 1414
0.2598
                                                                                                                          Reference
             Brooke et ol.  1986
                                                        Brooke et al. 1986
                                                                  SALTIMTEH SPECIES
                Mysid.                     LC
                Aconthomys i s  sculpto
                                                 0.09-0.19
                                                  0.1308
                                                        Dav i dson  et  al   I986a,b
N)
                  LC =  life-cycle  or  partial  life-cycle; ELS = early life-stage.

                  TBTO  =  tr i butyl t i ii  oxide.   Percent purity  is given in parentheses «hen available.

                  Measured  concentrations  of  the tributyltin cation.

                  The test  organisms  »ere  exposed to leachate from panels coated vith antifouling paint containing a tributyltin
                  polymer and  cuprous oxide.  Concentrations of TBT »ere measured and Davidson et al.  (I986a) demonstrated that the TBT
                  in the  leachate  had the  same toxicity as TBT alone.
-------
Table 2. (co*ti*ved)

                                 »cute-Cliro»ic iotio
                                 «s       *e«t« ¥«(«•      Ckratic ««U«
                            CaCOjl           « I •* pfonelas

Uysid.                         -               0 61°           O.IJ08            4 664
Acanthoaysis sculpto
  Reported by Valkirs et al   (I985a)
-------
                                  T*ki* 3.   Railed  C**«s  H*«*  Ac«t« Val*«s •Mb Sp*ci*$ M«a» Acute-Chronic Ratios

                                      (••us M««i                                    Sp«ci«s !!«*•           Species H*«*
                                      Acute ¥•!••                                   Ac«t« V«l««            Acnt«-Cbro«ic
                                        |M/!>            Sp.cies                       (m/L>h                  B«tioc

                                                                rBESH»ATEB SPECIES

                                         10.2            Mosquito.                       10.2
                                                         Culex sp.

                                          S.S            Channel  catfish.                 55
                                                         Ictolurus  panctotus

                                          S.4            Annelid,                         54
                                                         Lunbri culus vorIeqotus

                                          43            Cladoceran,                     43                  30 41
                                                         Ootthniq  moqna
                        4                  3.9             Rainbo*  trout.                   3.9
do                                                       So I BO  qqirdneri

                        3                  37             A«phipod,                        37
                                                         CoMnorus pseudolinnaeus

                        2                  26             Fathead ninnoi.                  2.6                  10.01
                                                         Pinepholes  promelas
             •
                        I                  05             Hydrq,                           0.5
                                                         Hydro  |p.
-------
Teble 3.

                Genus Meen                                     Species  Ueen           Species Vean
                Acate Velne                                   Acute Velee            Acute-Chronic
Heet*             b                 »etiec

                                           SALTKATtK SPECIES

  18            204.4              European flat  oyster,          204 4
                                   Ostreo edtil is

  17             83.28             Shore crab,                     83 28
                                   HeMiqropsus  nudus

  16             34.90             Mud crob.                       34.90
                                   Rhithroponopeus horrisi i

  15             23.36             yuMMichog,                      23 36
                                   Fundulus heteroclitus

  14            >I4 60             AMphipod,                      >I4.60
                                   Orchestic  trostiono

  13              9 732            Shore crab.                      9 732
                                   Corcinus Moenos

  12              6.812            Polychaete.                      6.812
                                   Meanthejs orenoceodentalo

  II              2.315            Sheepshead  Minno»,             2.315
                                   C»ori nodon vorieqotus

  10              2.238            Blue Mussel.                     2 238
                                   Kvtilus  edulis

   9              22              Copepod,                         22
                                   turyteMoro offInls
-------
                     Table 3.  (coetieued)
                                     Ceevs ilea*
                                     Acute «•!»•
                                       1.911
Copepod,
Mi tocro spi nipes
                           Species Mea*
                           Acute Value
 I .911
                   Species  Ueae
                   Acute-Chromic
                       Ratio6
                                       I. 745
                                       1.460
American lobster,               1.745
Hoiiorus omericonus

Chinook salnon.                 I.460
Oncorhvnchus tshonytschq
                                        .365
Hard clan,
Mercenorio mercenorio
 I  365
OJ
o
                                       1.204
Pacific oyster,
Crossostreo qiqos

Eastern oyster,
Crassostreo virqinico
 1.557
                                                                                        0.9316
                                       0.9732
Uysid,
UetomvsIdopsis elonqota
<0.9732"
                                       0.6326
                                       0.61
Copepod,
Ocort io tonsq

Uysid,
Aconthihiys I s sculpto
 0.6326
 0.61
                                                                                                            4.664
                       Ranked from most  resistant  to most  sensitive based on Genus Mean Acute Value.
                       From Table I
                     g  From Table 2.

                       This nas  used  as  the Genus  Mean  Acute Value in the calculation of the Final Acute Value
                       This »os  the  latest  concentration  used  in  the toxicity  test  and it killed 63Z of the exposed  mysids
-------
TafcU 3. (co.ti««*4)





fr«sh
     final AcuU Valu* = 0.2972




         final Acute-Chronic Ratio = 1 1 24    (s«* Uxt)




           Chronic Vain* = (0.2972 /i9/L) / 1 1 . 24 - 0.02644 /j9/L
Solf
     final Acit* Valu* = 0.5313




         final  Acutn-Chronic Ratio = 1 1  24    (s«» t«xt)




     final Chronic Valu* * {0.5313 /j9/L) / 11.24 * 0.04727




     final Chronic Valuo > O.OIO/J9/L    (lovorod to protect molluscs; s»* t«xt)
-------
T«bi* 4.   Toxicity of  Tribvtylti* to Azotic  Pi«»ts
Duretio«
                                                        Coocootrotio*
                                                                           Beferenco

Algo.
Bun) 1 lor i ODS i s filiforais
Alga.
Klebsorai di urn mor i num
Algo,
Monodus subterroneus
Algo,
Rophi doneao lonqiseto
Alga,
Tr i boneno aequole
Blue-green alga.
Osci 1 Utorio sp.
Blue-green alga,
Svnechococcus leopol iensis
Croon olga,
Chla»vdo«onas dvsosmos
Green alga,
Chlorel 1 a emersoni i
Green alga.
tfirrhnnrtal l/i rnninrin

TITC
TITC
TITC
TITC
TBTC
TBTC
TBTC
TBTC
TBTC
TBTC
fBESHWATEB SPECIES
14 No growth 1114
14 No growth 222 8
14 No growth 1.782 2
14 No growth 56. 1
14 No growth 1114
14 No growth 222 8
14 No growth 1114
14 No growth 1114
•
14 No growth 445.5
14 No growth 1114

Blanck 1986;
Blanck et al .
Blonck 1986;
Blanck et al
Blanck 1986;
Blanck et al
Blanck 1986.
Blonck et al
Blanck 1986;
Blonck et al
Blanck 1986,
Bl anck et al
Blanck 1986;
Blanck et al
Blanck 1986,
Blanck et al .
Blanck 1986;
Blonck et al
Blanck 1986;
Bl anck et al
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
                                                                                          1984
-------
T«bi* 4.  (continued)
Green alga,
tlonorophidium pusi 11 urn

Grean alga,
Scenedesmus obtusiusculus

Green alga,
Selenastrum copricornutum
C«e«icel*

 TITC


 TITC


 TITC
Herdness
      as
                                                CeCOjl
                                                                ••ratio*
                                                                    (4
                                                                    14
                                                                    14
No growth
No groith
                Co«c*«tratio«
Effect

No growth           1114
                                                    445.5
                                                                                                    1114
Blanck  1966;
Blanck  et al. 1984

Blanck  1986;
Blonck  et al. 1984

Blanck  1986;
Blanck  et al. 1984
                                                              SALTMATE8 SPtCltS
Diatom,
Skeletonemq costatum
Diatom,
Skeletonema costatum

Diatom,
Skeletonema costotum

TBTO

TBTO 3QC
(BioiUt Red)

TBTO 30C
(olkyl source)

5 Algistotic
algicidal
14 CC50
(dry cell
•eight)
14 CCSO
(dry cell
•eight)
0.9732-17 52 Thain 1983
>I7.52
1 >O.I2I6; <0.2433 CG«G Bionomics I98lc


0 06228 £C*G Bionomics I98lc


  TITC > tributyltin chlorida;  TBTO = tributyltin oxid*.  (arcant purity is givaii it paranthasas «ha« avqilabia
                                                         ' ' -v«

  Concantration of tha tributyltin cation, not th* chamical.  If tha concentrations **rt not maasurad and tha published results iere not
  raport*d to b* adjusted for purity, tha published rasults ••(•• •vltipliad by tba purity if it 
-------
                                   T«fcl« 5.   tfo«ccwMl«iie«  af  Tri»«tyiti* if Aquatic 0rf««i$Bs
Sal i«ity
S..ci«s £l«iSli! ll/iii

Green alga, TITO
Auk istrodesmus f olcatus


Coiceetretio*
, „ i /, »k
!• V«t«r lii«/LI
fBESOTATEB
52
47
21
15
••ratio*
(4a«s) Tissv*
SPECIES
7
14
21
28
•cr or
_!*£!_
300
253
448
467
                                                                                                                      B«f«re«c«
                                                                                                                       Maguire  «t al.  1984
                                                              SAtmiEi SPECIES
     MUSS«I

y*ti I us edulis

Pacific oystar,
Crgssostreo qiqos

Pacific oyst*r,
Crossostrea qiqas

Pacific oyster,
Crassostreo qiqos
Pacific oyst«r,
Crassostreo qiqas

Pacific oyster.
Crossestr«o qiqos

European
flot oyster,
OsIreo eduli s
                          TITO
                          TITO
T8TO
TITO
TBTO
                                        28.5-34.2
                28-31  5
                28-31  5
                                        28.5-34.2
                                          29-32
                                          29-32
                                          28-31  5
024 45 Soft 6,833*
parts
1.216 21 Soft 1,674*
parts
0.1460 21 Soft 6,047*
parts
0.24 45 Soft 7,292*
parts
1.557 56 Soft 2,300
parts
0 1460 56 Soft 11.400
parts
1.216 21 Soft 960*
parts
Thain and
laldock 1985
Thain 1986
Wai dock
et al 1983
Waldock
•t al 1983
Thain and
Waldock 1985
Thain 1986
Waldock and
Thain 1983
Waldock and
Thain 1983
Waldock
et al 1983
-------
Te»Ie S. (continued)
Seecies
European
flat oyster,
Ostrea edul is
European
flat oyster,
Ostrea edul is
European
flat oyster,
Ostrea edul is
European
flat oyster,
Ostreo edul is
1.1
Seiititf C«*c*«tr«ti0B Burnt ion
Cko*icel* Lfiilj L§ Ilil£ Lttl/iJL tiilii Tissee
TBTO 28-34.2 024 75 Soft
parts

TBTO 28-34.2 2 62 75 Soft
parts

4 28.5-34 2 0 24 45 Soft
parts

4 215-34.2 2 62 45 Soft
parts

BCr or
BAFC Reference
875* Waldock
et al 1983;

397* Thain 1986


1 ,167* Thain and
Waldock 1985;
Thain 1986
192.3* Thoin and
Woldock 1985;
Thain 1986
  TBTO = tributyltin oxide.  Percent purity is  given  in  parentheses  vhen available.

  Measured concentration of the tributyltin cation.

c Bioconcentration factors (BCFs) and biooccumulation  factors  (BAFs)  are based  on  measured  concentrations  of  the  tributyltin cation
  in voter and in tissue.

  Test organisms *ere exposed to leachate from  panels  coated  •ith  antifouling paint  containing  tributyltin.
f
BCfs »ere calculated based on the increase above  the  concentration  of  TBT  in  control  organises.>

Steady-state not reached.
-------
                                TeM« 6.   Other  Dot*  o*  Effects of Tributyltii o* Aquatic
Species
Algae.
Natural assenblge

Blue-green alga,
Anoboeno fIos-aquoe

Green alga,
Ant istrodesmus folcotus
Green alga,
Scenedesmus quodricaudo

Clom (larvo),
Corbi cula fIumi neo

Clodoceran,
Oophnio moqna

Cladoceran (<24 hr),
Oophnio moona
Clodoceran (<24 hr),
Oaphnio moqno

Cladoceran (adult),
Daphni a moqno

Rainbow trout (yearling),
Solmo go i rdnerI
Che«icgl'
  TBTO
  TBTC
  TBTO
  TBTC
  TBTO
Kardeess
(.g/L «s
_c«co3J_

_

_

_


_

-


200

200

_

_



Duration
FRESHWATER SPECIES
4 hr

4 hr

4 hr


4 hr

24 hr
24 hr

24 hr

24 hr

8 days

24 hr
48 hr


Effect

ECSO
(product ion)
ECSO
(reproduction)
ECSO
(product i on)
(reproduct ion)
ECSO
(product i on)
ECSO
LCSO

ECSO
(nobility)
ECSO
(•ability)
Altered
phototax is
LCSO


Concentration
(u«/LI


5

13


20
5
16

1,990
3

116

13.6

0.4S

25 2
189


Reference

Wong et al
1982
Wong et al .
1982
Wong et al .
1982

Wong et al .
1982
Foster 1981
Polster and
Halacha 1972
Vi ghi and
Calamari 1985
Vi ghi and
Calamari 1985
Header 1986

Al abaster
1969
-------
Table 6. (co*tiaued)
Hardiess
(•0,/L €S
Species Chemical" CeCOjl
Rainbow trout, TBTO
So Imp qoirdneri
Rainbow trout (embryo, larva), TBTC 94-102
Sal mo qairdneri




Frog (embryo, larva), TBTO
Rang temporal- i o
TBTF
TBTO

TBTF



Co«ce»trat io*
Duratioi Effect (u«/Llk
24 hr ECSO
(rheotaxis)
1 10 days 20Z reduction
in growth
23Z reduction
i n growth; 6. 61
mortal i ty
1001 mortality
5 days LC40
5 days LC50 >
5 days Loss oF body
water
5 days Loss of body
water
30 8

0.18
0 89


4 46
28 4
28.2
28 4

28.2


Refereece
Chi iamovi tch
and Kuhn 197?
Sei nen et ol .
1981




Laughl in and
Linden 1982





-------
     Table 6.  (co»tinned)
     Spec i es
     Natural  nicrobial
     populat ions
oo
     Natural  nicrobiol
     populat ions
Green alga,
Oonoli el>a sp.

Green alga,
Dunoliella sp.

0 i a t om,
Phoeodoctvlurn
tricornutum

D i a t om,
SVel atonema
cqstotum

Diatom,
Steletonemo
costotum
                                    Cneaical
                                      TBTC
                                           TBTC
                                           TBTO
                                           TBTO
                                           TBTO
                                           TBTA
                                           TBTA
Salinity
-------
Table 6.  (continued)

Spec i es
Diatom,
Skeletonema
costatum
0 i o t o* ,
Skeletonema
costatum
Di atom,
Skel etonema
costatum
Diatom,
Skeletonema
costotum

Di atom,
Skeletonema
costatum
D i a t om ,
Skel etonemo
costatum
Diatom,
Thalassi osi ra
pseudonana
Diatom,
Thalassi as i ra
pseudonana
Sal ini ty
Chemical" (a/ka)
TBTO 30


TBTO 30


TBTC 30


TBTC 30


•
TBTF 30


TBTF 30


TBTA 30


TBTO 30


Concentration
Duration Effect (««/L)k
72 hr EC50 0.3212
(populat ion
growth)
72 hr LC50 13 82


72 hr EC50 0 3207
(populat i on
growth)
72 hr LC50 10 24


'
72 hr EC50 >0 2346,
(population <0 4693
growth)
72 hr LC50 11.17


72 hr EC50 I.IOI
(population
growth)
72 hr EC50 1.002
(popul at i on
growth)

Reference
Walsh et
1985

Walsh et
1985

Walsh et
1985

Walsh et
1985


Walsh et
1985

Walsh et
1985

Walsh et
1985

Walsh et
1985



al


al


al


al



al


al


al


ol


-------
Table 6.  (continued)
Species
Dinof lagel late,
Cymnodi ni urn
sjlendens
Dogihelk (adult),
Nucello lapillus


Uud snai 1 (adult) ,
Nassari us
ofasolet us
O Blue mussel (spat) ,
Myt i lus edul is
Bl ue mussel (spat ) ,
Myt i lus edul is
Blue mussel ( larva) ,
Myti lus edul is
Blue mussel (juvenile),
Myti lus edulis
Salinity Concentration
Chemical" (a/ke.) Duration Effect (ua/L)b
TBTO - 72 hr 1 OOZ 1 .460
mortal i ty
c - 120 days 4IZ Imposex 0 05
(superimposition
of male anatomical
characteristics on
f ema 1 es )
TBTO 23 35-75 Imposex
days
c 28.5-34 2 45 days Significant 0.24
reduction in
growth; no
mortal i ty
c 28 5-34.2 45 days 1 OOZ 26
mortal i ty
TBTO 33 15 days 5IZ mortality; 0.0973
reduced gro«th
TBTO 33.7 7 days Significant 0 3893
reduction
in growth
Reference
Solazar 1985
Bryan et al .
1986

Smith 1981
Tha i n and
Waldock 1985
Tha in 1986
Tha i n and
Waldock 1985
Thain 1986
Beaumont and
Budd 1984
Stromgren
and Bongard
1987
-------
Table 6.  (continued)
Spec i es
Bl ue mussel
(25 to 4.1 cm).
Uyt i lus edul is
Blue mussel
(2.5 to 4.1 cm),
Mytilus edulis
Pacific oyster (spot),
Crossost reo qi qos
Pacific oyster (spat),
Crossostreo aiqos
Pacific oyster (spat),
Crossostreo qiqos
Pacific oyster (spot),
Crossostreg qi qos
Pacific oyster (larva),
Crossostreo qiqos
Pacific oyster (larva),
Crossost red qi qos
Pacific oyster (larva),
Crossostreo qi qos
Selinity
Chemical* (a/kg) Ouretion
c - 66 days
c - 66 days
c 28.5-34.2 45 days
c 28.5-34.2 45 days
TBTO 29-32 56 days
TBTO 29-32 56 days
c 30 days
c - 113 days
TBTF 18-21 21 days
Concentration
Effect («a/L)k
LC50 0 97
Significant 0.31
decrease in
shell growth
40Z mortality; 0 24
reduced growth
90Z 26
mortal i ty
No growth 1.557
Reduced growth 0 1460
1 OOZ 20
mortal i ty
30 Z mortality 0.2
and abnormal
•
development
Reduced number 0 02346
of normally
developed
larvae and
setting of spot
Reference
Valkirs et al
! 985o,l887
Volkirs et al.
I985a
Thain and
Waldock 1965;
Thain 1986
Thain and
Waldock 1985
Waldock and
Thain 1983
Waldock and
Thain 1983
Al zieu et al
1980
Al zi eu et ol .
1980
Springborn Bionomics
I984a
-------
Table 6.  (continued)
Species
Pacific oyster (larva),
Crossostreo qi qos
Pacific oyster (embryo),
Crossostreo qiqos

Pacific oyster (embryo),
Crossostreo oi gas
Pacific oyster (larva),
Crossostreo qiqas
Pacific oyster (larva),
N> Crossostrea qiqas
Eastern oyster (2 7-5.3 cm),
Crossostrea vi rqi ni eg

Eastern oyster (2.7-5.3 cm),
Crossostreo vi rqinico
Eastern oyster (adult),
Crossostreo vi rqi ni co
Eastern oyster (adult),
Crossostreo vi rqi ni co
Eastern oyster (embryo),
Crossostrea vi rqi ni co
European flat oyster (spot),
Oslreo edul is

Salinity Coiceatrat ion
Chemical" (a/ka) Duretio. Effect («a/Lik
TBTf 18-21 15 days 1 OOX mortality 0.04692

TBTA 28 24 br Abnormal devel- 4304
opment ; 30-40Z
mortal i ty
TBTA - 24 hr Abnormal 0.8604
development
TBTA - 24 hr Abnormal 0.9-4
development
TBTA - 48 br 1 OOZ mortal i ty 2581
67 days Decrease in 0.73
condition index
(body (eight)
* - 67 days No effect 1 89
on survival
c 33-36 57 days Decrease in O.I
condition index
c 33-36 30 days LC50 25

TBTC 18-22 48 hr Abnormal shell 0.77
development
TBTO 30 20 days Significant 0 01946
reduct ion
in growth
Reference
Springborn Bionomics
I984o
His and Robert 1980


Robert and
His 1981
Robert and
His 1981
Robert and
His 1981
Volkirs et at
I985a

Valkirs »t al
I985a
Henderson 1986

Henderson 1986

Roberts, Manuscript

Thai a and
Waldock 1985

-------
Table 6.  (continued)
Speci es

European flat oyster (spat),
Ostreo edulis
European flat oyster (spat),
Ostreo edulis
European flat oyster (adult),
Ostreo edulis
European flat oyster (adult),
Ostreo edulis
European flat oyster (adult),
Ostreo edulis
Hard clam (post larva),
Mercenorio mercenorio
Hard clan (post larva),
Uercenorio mercenori a
                                    Chemical'
                                      TBTC
                                      TBTC
                                      (95X)
Salinity
 (a/fc«)

28.5-J4.2
                                                     28.5-34.2
                                                       28-54
                                                       28-34
                                                       28-34
Duration
45 days


45 days


75 days



75 days



75 days


96 hr


96 hr




Concent rat ioi
Effect («a/Uk
Decreased 0.2392
groith

702 Mortality 26


Complete 0 24
inbibi t ion
of larval
product ion
Retardation 0.24
of sex change
from «ale to
female
Prevented 26
gonadal
development
Inhibited 0 0007330
swimming
behavior
Reduced 0.002922
number of
animals
develop! ng
a foot
Reference
Thain and
Woldock 1985;
Thain 1986
Thain and
Waldock 1985;
Thain 1986
Uata 1986



Thain 1986



Thain 1986


Becerra-
Huencho 1984

Becerra-
Huencho 1984



Hard clam (embryo, larva),
Mercenori o mercenaria
                                      T6TO
                 14 days      Reduced growth    O.Q25
                                                                                                                        Laugh!in  et  al
-------
Table 6. (co»ti«ued)
Species
Hard clam ( larva) ,
Uercenaria mercenaria
Hard clam (post larva),
Uercenorio mercenoria
Hard clam ( larva) ,
Uercenaria mercenaria
Clam (adult),
Protothaca stamina
Copepod ,
Eurvtemora affinis
Copepod,
Eurvtemora affinis
Copepod ,
Acart i a tonso
Ampbipod (larva, juvenile),
Gommarus oceanus
Amphipod (larva, juvenile),
Gammarus oceanus
Amphipod (larva, juvenile),
Gammarus oceanus
Amphipod (larva, juvenile),
Canmiarus oceanus
Chemical"
TBTO
TBTO
TBTC
TBTO
TBTC
TBTC
TBTO
TBTO
TBTf
TBTO
TBTF
Saliiity Co«ce«trat ioi
(q/kal Duratio* Effect .2 920
|Q. 3 13 days Reduced survival 0 088
of neonates and
adults
14.6 13 days Reduced survival 0.224
of neonates
144 hr EC50 0 3893
7 8 »k IOOZ mortality 2.920
*
7 8 »k IOOZ mortality 2 816
7 8 »k Reduced 0.2920
survi val
and growth
7 8 «k Reduced 0 2816
surv i val and
Reference
Laughlin et al . 1987
Laughlin et al . 1987
Roberts, Uanuscript
Salozor and
Salazar, Uanuscript
Hal 1 et al . Uanuscri pt
Hal 1 et al . , Uanuscript
U'ren 1983
Laughl in et al .
19846
Laughl in et al .
19846
Laughl in et al .
19846
Laughl in et al .
19846
                                                                                   i ncreased grovt h
-------
Table 6.  (continued)
Species
Amphipod (adul t ) ,
Or chest io trask iano
Amphi pod (adul t ) ,
Orchest i a trosk i ono
Crass shrimp,
Paloeroonetes puqio
Uud crab (larva),
Rh i throponopeus horri s i i
Uud crab ( larva) ,
wn Rh i throponopeus horri s i i
Uud crab ( larva) ,
Rhi throponopeus harrisii
Uud crab ( larva) ,
Rhi throponopeus horri si i
Uud crab,
Rhi thropanopeus horr isi i
Uud crab,
Rhi throponopeus horrisi j

Uud crab,
Rhi throponopeus horri s i i
Chemical"
TBTO
TBTF
TBTO
(95X)
TBTO
TBTS
TBTO
TBTS
TBTO
TBTO

TBTO
Salinity
(q/ka)
30
30
99-112
15
15
15
15
15
' V.
15

15
Ourat ion
9 days
9 days
20 min
15 days
15 days
15 days
15 days
6 days
6 days

6 days
Concentration
tflect (««/L)k
Approx BOX 9.732
mortal i ty
Approx 90Z 9.732
mortal i ty
No avoidance 30.
Reduced 1 4 60
developmental
rate and growth
Reduced 18.95
developmental
rate and growth
63X mortality >24.33
74X mortality 28.43
BCf=24 5.937
for carapace
BCf=6 5 937
for hepato-
pancreas
BCF=0 6 5.937
for testes
Reference
Loughl i n et al .
1982
Laughl in et al .
1982
Pinkney et al . 1985
Laughl in et al .
1983
Loughl in et al .
1983
Laughl in et al
1983
Laughl in et al .
1983
Evans and
Laughl in 1984
Evans and
Loughlin 1984

Evans and
Loughl in 1984
-------
Table 6.  (continued)
Species Chemical0
Uud crab, TBTO
Rhi throponopeus horrisi j
Uud crab. TBTO
Rhi throponopeus horrisi i
Fiddler crab, TBTO .
Uco puqi later
Atlantic menhaden (juvenile), TBTO
Brevoortio tyrannus
** Chinook salmon (adult), TBTO
Oncorhvnchus tshowvtscho
Chinook salmon (adult), TBTO
Oncorhynchus tshowvtscho
Chinook salmon (adult). TBTO
Oncorhvnchus tshowytschq
Uummichog, TBTO
Fundulus heteroclitus (95Z)
Col i f orni a gruni on c
(gamete through embryo),
Leuresthes tenuis
Col i f orni a grun i on c
(gamete through embryo),
Salinity Concentration
(a/kq) Duration Effect (j<«/L)b
15 6 days BCF=4I 5.937
for gill
tissue
15 6 days 8CF=I .5 for 5.937
chelae muscle
25 £24 days Retarded limb 05
regeneration and
molt i ng
9-11 - Avoidance 5.437
28 96 hr BCF=4300 1.49
for liver
28 96 hr BCF=I300 1 49
for brain
28 96 hr ICF=200 1 49
for muscle
9.9-11.2 20 min Avoidance 3.7
10 days Significantly 014-1 72
enhanced
growth and
hatching success
10 days 50Z reduction 74
i n hatch i ng
Keference
Evans and
Laughlin 1984
Evans and
Laugh! in 1984
Weis et ol . 1987
Hall et al .
1984
Short and Thrower
I986a,c
Short and Thrower
I986a,c
Short and Thrower
I986o,c
Pinkney et al . 1985
Newton et al .
1985
Newton et al .
1985
Leuresthes tenui s
-------
Table 6. (continued)
Species
California grunion (embryo),
leuresthes tenuis



California grunion (larva),
Leuresthes tenuis


Striped bass (juvenile),
Uorone saxat i 1 is
Speckled sanddab (adult),
Chi thari chthvs stiamaeus

Salinity Concentration
Chemical" (a/kq) Duration Effect (pa/l)k
c - lOdoys No adverse 014-1.72
effect on
hatch! ng
success or
growth
c 7 days Survival 0 14-1 .72
increased as
concentrat i on
i ncreased
TBTO 9-11 - Avoidance 24 9
(951)
TBTO 33-34 96 hr LC50 18 5
*
Reference
Newton et al .
1985



Nenton et al .
1985


Hall et al
1984
Salazar and Solazar,
Uanuscr i pt
0 TBTA = tributyltin  acetate; TBTC = tributyltin chloride; TBTF = tributyltin fluoride; TBTO = tributyltin oxide;
  TBTS = tributyltin  sulfide.  Percent purity  is given  in parentheses when available.

  Concentration  of  the  tributyltin cation, not the chemical.  If the concentrations Mere not measured and the published  results  nere not
  reported  to be adjusted  for purity, the published results were multiplied by the purity if it was reported to be less  than  95*.

0 The test  organisms  were  exposed to leachate  from panels coated «ith antifouling paint containing tributyltin.

  The test  organisms  were  exposed to leachate  from panels coated «ith antifouling paint containing a tributyltin polymer
  and cuprous oxide  Concentrations of TBT «ere measured and Davidson et al. (I986o) demonstrated that the TBT in the leachate  had
  the same  toxicity as  TBT alone.
-------
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fungicides, wetting  agents and miscellaneous substances.  Int.  Pest  Control




11:29-35.








Allen, A.J., B.M. Quitter and C.M. Radick.  1980. The  biocidal  mechanisms  of




controlled release bis(tri-n-butyltin)  oxide in Biomphalaria  glabrata.  In:




Controlled release of bioactive materials.  Baker, R.  (Ed.). Ac.ademic Press,




New York, NY.  pp. 399-413.









Alzieu, C. 1986. The  detrimental effects on oyster culture  in  France -




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DC. pp. 1130-1134.









Alzieu, C., Y.  Thibaud, M. Heral and B. Boutier. 1980. Evaluation of the  risks




of using antifouling  paints near oyster zones. Rev. Trav.  Inst. Peches Marit.




44:301-348.








Barug, D. 1981. Microbial degradation of bis(tributyltin) oxide. Chemosphere




10:1145-1154.








Beaumont, A.R.  and M.D. Budd. 1984. High mortality of the  larvae of the common




mussel at low concentrations of tributyltin. Mar. Pollut. Bull. 15:402-405.
                                       48
-------
Becerra-Huencho,  R.M.  1984. The effect of organotin and copper sulfate on the



late development and presettlement behavior of the hard clam Mercenari a



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Blair, W.R., G.J. Olson, F.E. Brinckman and W.P. Iverson. 1982. Accumulation



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Blanck, H.  1988.  University of Goteborg, Goteborg, Sweden. (Memorandum to




D.J. Call,  Center for Lake Superior Enviromental Studies, University of




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Blanck, H., G. Wallin and S.A. Wangberg. 1984. Species-dependent variation  in




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Brooke, L.T.,  D.J. Call, S.H. Poirier, T.P. Markee, C.A. Lindberg. D.J.




McCauley and P.G. Simonson. 1986.  Acute toxicity and chronic effects of




bis(tri-n-butyltin)  oxide to several species of freshwater organisms. Center



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