Note:
This is not an exhaustive list.
When time allows more information will be added.
Quinoxyfen
-
Fungicide -
CAS No. 124495-18-7
Examination and possible
vote on a draft Commission Decision making it possible for Member
States to extend provisional authorisations granted for the new
active substances carfentrazone, cinidon-ethyl, cyhalofop-butyl,
ethoxysulfuron, famoxadone, flazasulfuron, flufenacet, flumioxazine,
flurtamone, fosthiazate, isoxaflutole, metalaxyl-M, Pseudomonas
chlororaphis, quinoxyfen, Spodoptera
exigua nuclear polyhedrosis virus and sulfosulfuron (SANCO/3963/2001
rev 6).
... Sweden supports
a decision of non-inclusion of quinoxyfen in Annex I to Directive
91/414/EEC. The possible environmental impact of quinoxyfen cannot
be shown to be acceptable with sufficient security. This is due
to the high persistence, high potential
for bioaccumulation and indicated potential for long-range transport.
Substances like quinoxyfen may accumulate in various environmental
compartments, including biota, and the effects of such accumulation
are unpredictable. The Swedish opinion is that whatever
the final results of the additional, ongoing study on organic
matter breakdown may be, those results cannot be sufficient to
demonstrate an acceptable impact.
Ref:
SHORT REPORT OF THE MEETING OF THE STANDING COMMITTEE ON PLANT
HEALTH HELD ON 7 DECEMBER 2001 IN BRUXELLES. SCPH 5/01. European
Commission.
http://www.fluorideaction.org/pesticides/quinoxyfen.eu.dec.7.2001.pdf
Silafluofen
- Insecticide - CAS No. 105024-66-6
Classified
as a "severe marine pollutant".
Ref: Transport Canada. APPENDIX 1 MARINE
POLLUTANTS. Online March 24, 2003.
http://www.tc.gc.ca/acts-regulations/general/t/tdg/regulations/tdg001/part_2.htm
Sodium
Fluoride - Wood Preservative, US
EPA List 4B Inert
- CAS No. 7681-49-4
Effects
of Fluoride on Fish Passage.
The
upstream migration of adult spring chinook
salmon in the Columbia River has been subject to unusually
long delays at John Day Dam. During the spring migration period,
average passage times for radio-tagged salmonids at John Day Dam
were 158 and 156 hours in 1979 and 1980, respectively. In contrast,
average passage time at Bonneville Dam was less than 48 hours
and at The Dalles Dam it was less than 24 hours. In addition,
passage times for salmonids in the fall of 1982 were twice as
long at John Day Dam as they were at The Dalles and McNary Dams.
The delay of nearly 1 week at John Day Dam appeared to contribute
to increased mortality and may have affected the spawning success
of migrating adult salmonids.
...In
1982, preliminary studies conducted by CZES Division personnel
assessed the distributions of many pollutants near John Day Dam.
The results of this investigation suggested that the fish-passage
delays might be related to contaminants discharged at an aluminum
smelter outfall located on the Washington shore 1.6 km upstream
from John Day Dam. In
particular, high concentrations of fluoride in the vicinity of
John Day Dam (0.3-0.5 mg/L in 1982) prompted investigators to
focus sampling and research efforts on this contaminant.
In 1983 and 1984, behavior
tests were conducted in which over 600 returning salmonids (chinook,
coho, and chum, O. keta, salmon) were captured and tested with
different concentrations of fluoride in a two-choice flume located
in the spawning channel of Big Beef Creek, Washington. The
conclusion from these experiments was that the behavior of upstream-migrating
adult salmon would be adversely affected by fluoride concentrations
of about 0.5 mg/L and that concentrations of 0.2 mg F/L were at
or below the threshold for fluoride sensitivity of chinook and
coho salmon.
Beginning in 1983 and
continuing through 1986, fluoride discharges from the aluminum
plant were greatly reduced. This was initially due to modifications
in the plant's pollution-discharge system. However, it was also
during this period that the Washington Department of Ecology (WDOE)
took an active interest in the results of the CZES Division's
water quality and behavior tests. The WDOE
lowered significantly the discharge limitations for a number of
contaminants, including fluoride, in the aluminum plant's wastewater
discharge permit. With the reduction in fluoride discharged from
the aluminum plant, there was a corresponding drop in fluoride
concentrations in the river near the outfall and John Day Dam.
Concurrently, fish passage delays and interdam losses of adult
salmon decreased to acceptable levels.
Ref: April 1993. NOAA
Technical Memorandum NMFS-NWFSC-7. Coastal Zone and Estuarine
Studies Division. RESEARCH ACTIVITIES AND ACCOMPLISHMENTS. 1980-89.
Edited by Douglas B. Dey. National Marine Fisheries Service, Northwest
Fisheries Science Center, Coastal Zone and Estuarine Studies Division,
2725 Montlake Blvd. E., Seattle WA 98112
[Earthworms].
The impact of four fluorides (NaF, KF, FCH2COONa
[Sodium fluoroacetate] and CaF2) in sublethal concentrations on
the earthworm Eisenia fetida was investigated (model experiments)
in relation to its growth, maturity (clitellum-development) and
fertility (number of cocoons and number of hatchlings). Fluoride-accumulation
was determined at the end of the 22 weeks' test period. In higher
concentrations NaF, KF and FCH2COONa reduced growth of
E. fetida significantly. CaF2 had no effect. The
maturity was delayed through higher concentrations of NaF and
KF in the substrate. In the case of CaF2, most worms had
a fully developed clitellum. Most cocoons were found in the experiments
with FCH2COONa. Small concentrations of NaF, KF an FCH2COONa obviously
raised cocoon-numbers, whereas higher concentrations of NaF and
KF reduced it. Only NaF reduced the number
of hatchlings per cocoon significantly. At the end of the test,
all worms from the variants with NaF, KF and CaF2 had a significantly
higher fluoride [abstract truncated]
Ref: Influence of different fluorides in
sublethal concentrations on growth, fertility and fluoride-accumulation
of Eisenia foetida (Oligochaeta, Lumbricidae). [Earthworm]; by
VOGEL J, OTTOW J CG. PEDOBIOLOGIA; 36 (2). 1992. 121-128. [From
Toxline at Toxnet].
Sodium fluoroacetate
(Compound
1080)
- Insecticide, Rodenticide - CAS No.
62-74-8
Measured oral LD 50
values of fluoroacetate in the house sparrow,
redwinged blackbird, starling and golden eagle are 3.0, 4.22,
2.37, and 1.25 to 5 mg/kg, respectively. In addition, measured
acute toxicity data for mammalian wildlife include an oral LD50
of 0.22 to 0.44 mg/kg for mule deer,
an oral LD50 of 1.41 mg/kg for male ferrets,
and an oral LD 50 of 0.5 to 1.0 mg/kg for
bears. EPA believes that there is sufficient evidence for
listing sodium fluoroacetate on EPCRA section 313 pursuant to
EPCRA section 313(d)(2)(C) based on the environmental toxicity
data for this chemical.
Ref: USEPA/OPPT. Support Document for the
Health and Ecological Toxicity Review of TRI Expansion Chemicals.
U. S. Environmental Protection Agency, Washington, DC (1993).
As cited by US EPA in: Federal
Register: January 12, 1994. Part IV. 40 CFR Part 372. Addition
of Certain Chemicals; Toxic Chemical Release Reporting; Community
Right-to-Know; Proposed Rule.
Sodium fluoroacetate
(1080), (also known as sodium monofluoroacetate), is a fluorinated
carboxylic acid ester with high to very
high toxicity to birds and mammals.
Ref:
Australia. National Registration Authority for Agricultural and
Veterinary Chemicals. Reconsideration of products containing Sodium
fluoroacete (1080) and their labels. Background to the Review
and Scope Document.
http://www.fluorideaction.org/pesticides/1080.australia.july.2002.pdf
Sulfentrazone -
Herbicide - CAS No. 122836-35-5
Phototoxic
Pesticide.
Light-dependent peroxidizing herbicides (LDPHs).
US EPA identified the organofluorine herbicides
Acifluorfen, Azafenidin, Carfentrazone-ethyl, Flumiclorac-penty,
Flumioxazin, Fluthiacet-methyl, Fomesafen, Lactofen, Oxadiargyl,
Oxadiazon, Oxyfluorfen, Sulfentrazone,
Thidiazimin as phototoxic
pesticides that act by inhibiting protoporphyringen oxidase
in the heme and chlorophyll biosynthetic pathway.
[10 out of the 13 pesticides that EPA identified are organofluorines].
SEE
http://www.fluoridealert.org/pesticides/PHOTOTOXICITY.PAGE.htm
Ref:
December 11, 2001 - US EPA.
Revised Environmental
Fate and Effects Division Preliminary Risk Assessment for
the Oxyfluorfen Reregistration Eligibility Decision Document (also
at: http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxyefedchap.pdf
).
Persistent
in Soil.
Enviornmental Fate: A typical half-life
for sulfentrazone in soils is 541 days... Sulfentrazone's
potential to leach to groundwater is high; surface runoff potential
is high, and potential for loss on eroded soil is intermediate.
Ref:
Sulfentrazone. Roadside Vegetation Management Herbicide Fact Sheet.
Washington State Department of Transportation.
http://www.fluorideaction.org/pesticides/sulfentrazone.wa.state.facts.pdf
-- Environmental Characteristics.
Acceptable information from environmental fate studies with respect
to the persistence and mobility of sulfentrazone under laboratory
and field conditions has been reviewed. Based on the current environmental
fate data base, sulfentrazone has the following characteristics:
1) moderately soluble, 2) not susceptible to hydrolysis, 3) extremely
susceptible to direct photolysis in water, 4) very stable to photolysis
on soil, 5) aerobic half-life of 1.5 years, 6) anaerobic half-life
of 9 years, 7) very high mobility in soil (average Koc = 43, Kd
< 1), and 8) low volatility from soils and water. With these properties,
it appears that sulfentrazone is highly
mobile and persistent, and has a strong potential to leach into
groundwater and move offsite to surface water.
-- Potential to Contaminate Groundwater. A groundwater exposure
estimate for sulfentrazone was conducted based on findings from
a prospective groundwater monitoring study in North Carolina.
Although the study was incomplete, enough data were collected
to confirm that sulfentrazone leaches substantially
to groundwater in areas with sandy soils.
-- Aquatic. Sulfentrazone is practically non-toxic to the rainbow
trout (LC50 ) greater 120 ppm) and slightly toxic to the bluegill
sunfish (93.8 ppm). The results indicate that sulfentrazone is
slightly toxic to fish on an acute basis. The chronic results
indicate that sulfentrazone significantly affects young fish survival
and growth at aquatic concentrations as low as 5.93 ppm. Sulfentrazone
is slightly toxic to aquatic invertebrates on an acute basis.
The results from data from chronic freshwater invertebrates indicate
that survival of young daphnids is adversely
affected at sulfentrazone concentrations as low as 0.51 ppm.
The results from acute estuarine and marine animals study are
incomplete but indicate that sulfentrazone is
highly toxic to estuarine/marine organisms.
Ref: US EPA. Pesticide Fact Sheet. Sulfentrazone
Reason for Issuance: Registration of a New Chemical Date Issued:
February 27, l997.
http://www.epa.gov/opprd001/factsheets/sulfentrazone.pdf
Sulfluramid
- Acaricide, Insecticide - CAS No. 4151-50-2
As
a class, fluorinated organic compounds are resistant
to photolysis. If released to soil, sulfluramid is expected
to have no mobility based upon an estimated Koc of 3.5X10+6. Volatilization
from moist soil surfaces is expected to be an important fate process
based upon an estimated Henry's Law constant of 5.4 atm-cu m/mole.
However, adsorption to soil is expected to attenuate volatilization.
As a class, fluorinated organic compounds
are resistant to microbial degradation. [Giesy JP, Kannan
K; Environ Sci Technol 36: 147A-152A (2002)] If released into
water, sulfluramid is expected to adsorb to suspended solids and
sediment based upon the estimated Koc. Volatilization from water
surfaces is expected to be an important fate process based upon
this compound's estimated Henry's Law constant. However, volatilization
from water surfaces is expected to be attenuated by adsorption
to suspended solids and sediment in the water column. The
estimated volatilization half-life from a model pond is 107 years
if adsorption is considered. An estimated
BCF of 500 suggests the potential for bioconcentration in aquatic
organisms is high.
Ref: Hazardous Substances Data Bank for
SULFLURAMID CASRN: 4151-50-2.
http://www.fluorideaction.org/pesticides/sulfluramid.hsdb.oct.2003.htm
Ref:
Acute Aquatic Ecotoxicity Summaries for Sulfluramid
on All Taxa Groups . PAN Pesticides Database - Chemical Toxicity
Studies on Aquatic Organisms. http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC34496 |
Common
Name |
Scientific
Name |
Avg Species
LC50 (ug/L) |
LC50 Std
Dev |
Number
of Studies |
Avg Species
Rating |
Fish |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
210.0 |
- |
1 |
Highly
Toxic |
Fathead
minnow |
Pimephales
promelas |
5,054 |
4,866 |
2 |
Moderately
Toxic |
tau-Fluvalinate
- Acaricide, Insecticide - CAS No. 102851-06-9
--
Considerable accumulation of tau fluvalinate was observed in wax.
Depending on
the location of the samples tau fluvalinate concentrations varied
from 0.2 mg/kg - 5.5 mg/kg, with a maximum of 26.9 mg/kg in one
wax sample collected from a frame positioned next to a strip.
-- Accumulation in wax is the result of the stability of tau fluvalinate
in this matrix, its lipophilic character and the fact that wax
is normally reused over several seasons. Monitoring of tau fluvalinate
residues in honey and wax in Belgium in 1989-1992 revealed that
residues in wax increased exponentially
when the wax was reused over the years. Transfer of tau
fluvalinate residues from wax to honey was shown to be negligible.
However, the high tau fluvalinate residues in wax should be taken
into consideratin in the evaluation of tau fluvalinate since contamination
of honey with wax particles has to be expected (0.5 % content
of water insoluble particles in honey is allowed).
Ref:
Revised
Summary Report. EMEA/MRL/021-REV1/95. Committee for Veterinary
Medicinal Products. The European Agency for the Evaluation of
Medicinal Products.
http://www.fluorideaction.org/pesticides/tau.fluvalinate.1995.review.pdf
-- Environmental
hazards:
Toxic to aquatic organisms, may cause long-term adverse effects
in the aquatic environment.
-- Ecological Information:
Very toxic to aquatic organisms.
Ecotoxicity:
Fish: LC 50 > 0.024 mg/l, 96 hours (rainbow trout).
Algae: EC 50 = >100 mg/l (72 hours).
Daphnia: LC 50 = 0.011 mg/l (48 hours)
Ref: Material Safety Data Sheet for Klartan.
: Code no. R-10834.G. Makhteshim Agan (UK) Limited Unit 16, Thatcham
Business Village, Colthrop Way, Thatcham Berkshire RG19 4LW.
http://www.fluorideaction.org/pesticides/tau.fluvalinate.msds.klarta.pdf
Teflubenzuron
- Insecticide - CAS No. 83121-18-0
TOXIC chemicals used
on salmon farms could be killing off key elements of the marine
food chain, according to a report leaked to a leading scientific
magazine. "New
Scientist" magazine has obtained a copy of a 178-page report
which forms part of the ongoing 4 million study into the industry,
which was launched by the UK government in 1999.
In the leaked document it is alleged that chemicals such as cypermethrin,
azamethiphos or teflubenzuron are damaging
small crustaceans and other marine wildlife, which could be crucial
to the survival of other species. These chemicals are often
used by farmers to rid fish of sea lice.
- See also April 25, 2002
press release from Friends of the Earth, Scotland.
Ref: Leaked
Report Claims Toxins Are Hitting Marine Food Chain Fish Farming
Today- Fish Farming Today. April 25, 2002
-- There is very little
information available on the environmental fate and ecological
effects of teflubenzuron in aquatic environments. The specific
mode of action of teflubenzuron means it is highly
toxic to aquatic crustacean invertebrates, but low in toxicity
to fish, mammals and birds. As with emamectin benzoate, it is
likely that the sediments will act as a
sink for teflubenzuron and so sediment associated organisms
are more likely to be affected by this chemical.
-- It is difficult to predict the ecological risk of teflubenzuron
to the marine environment because of the current lack of information.
Results from field studies referred to in SEPAs environmental
risk assessment suggest that the use of
teflubenzuron for sea lice control may present a moderate to high
environmental risk. It seems unlikely that teflubenzuron
will be widely used for sea lice control in Scotland, but if use
does increase, investigation into the potential long-term impacts
of this chemical on the marine environment is recommended.
Ref:
REVIEW AND SYNTHESIS OF THE ENVIRONMENTAL IMPACTS OF AQUACULTURE.
The Scottish Association for Marine Science and Napier University.
Scottish Executive Central Research Unit. 2002.
http://www.scotland.gov.uk/cru/kd01/green/reia.pdf
Although teflubenzuron
is relatively non-toxic to most marine species (e.g. fish, algae,
shellfish), it is potentially highly toxic
to any species which undergo moulting within their life cycle.
This will therefore include some commercially important marine
animals such as lobster, crab, shrimp and some zooplankton species.
-- Subsequent chemical analysis confirmed that measurable
concentrations were generally not present in water after treatment
and that levels in sediments were variable but followed the predicted
dispersion model with measured levels of teflubenzuron extending
initially to about 50m from cages in line with the main direction
of current. In the study, teflubenzuron
was found to persist longer than 6 months, which was longer
than expected and hence additional studies were commissioned by
Nutreco at the request of SEPA and VMD. The predicted half-life
of teflubenzuron in sediment was from 8 to 92 days depending on
sediment type (Myrvold, 1997) and it had been expected that 90%
of teflubenzuron should have been degraded within 6 months. The
indication of a potential for longer persistence is attributed
to the site being a ieworst casels site already enriched and impacted
by organic wastes with teflubenzuron being retained by binding
with organic material (Trouw, 1999). The results from long-term
site monitoring finally reported a half
life of 104 to 123 days (Trouw, 1999). From this data,
SEPA now intend to apply a half life of 115 days as a decay factor
when undertaking site loading calculations for consent applications
or reviews.
-- Chemical analysis of samples collected on-site of indigenous
crustacea was also undertaken. It was concluded that there was
a risk that sediment dwelling crustacea, such as edible crab (Cancer)
and possibly Norwegian lobster (Nephrops), may accumulate teflubenzuron
from contaminated sediment. However, it is known that depuration
and loss of teflubenzuron does proceed following initial exposure
and uptake (McHenery, 1997) and hence levels may be lost from
such species before toxic effects occur (moulting).
-- The
half-life of teflubenzuron in sediment suggests that there is
a moderate risk of build up in sediment through repeat applications,
although the risk of this is reduced where fewer applications
are required by correct use of the product strategy.
Ref:
Calicide (Teflubenzuron) - Authorisation for use as an in- feed
sea lice treatment in marine cage salmon farms. Risk Assessment,
EQS and Recommendations (As agreed at the Board Meeting held on
7 th July, 1998 and subsequently updated in July, 1999). Policy
No. 29. SCOTTISH ENVIRONMENT PROTECTION AGENCY. Fish Farming Advisory
Group.
http://www.fluorideaction.org/pesticides/teflubenzuron.scotlandepa99.pdf
Tefluthrin
- Insecticide - CAS No. 79538-32-2
Aquatic acute toxicity
values for tefluthrin include a rainbow trout 96-hour LC 50 of
0.06 ppb, a bluegill 96-hour LC50 of 0.13
ppb, a sheepshead minnow 96-hour LC50 of 0.13
ppb, a daphnid 48-hour EC50 of 0.07
ppb, and a mysid 96-hour EC 50 of 0.053
ppb. EPA believes that there is sufficient evidence for
listing teflurin on EPCRA section 313 pursuant to EPCRA section
313(d)(2)(C) based on the available environmental toxicity data
for this chemical.
Ref: USEPA/OPP. Support Document for the
Addition of Chemicals from Federal Insecticide, Fungicide, Rodenticide
Act (FIFRA) Active Ingredients to EPCRA Section 313. U. S. Environmental
Protection Agency, Washington, DC (1993). As cited by US EPA in:
Federal
Register: January 12, 1994. Part IV. 40 CFR Part 372. Addition
of Certain Chemicals; Toxic Chemical Release Reporting; Community
Right-to-Know; Proposed Rule.
Tetraconazole
- Fungicide - CAS No. 112281-77-3
Threatened
and Endangered Species Concern in the US.
-- The black-footed ferret is possibly
collocated in a total of 13 counties in three states (MT, NE,
and WY) based on EFED‘s LOCATES Database. There may be a
potential for indirect adverse effects based on an endpoint of
increased length of gestation. It is possible that the availability
of prey for the black-footed ferret could be reduced. The
black-footed ferret feed on prairie dogs and other small mammals
that may chronically contain tetraconazole residues.
-- The US Fish and Wildlife Service is currently considering a
petition to delist the Preble‘s mouse.
This petition is based on the review of available information
which indicates that the Preble's mouse is not a discrete taxonomic
entity, does not meet the definition of a subspecies, and was
listed in error. Risk refinements will not be necessary if this
species is removed from the list. A final rule will be made in
May 2005 (FR Vol. 70. No. 21. February 2, 2005).
Ref: April 2005. Pesticide Fact Sheet:
Tetraconazole. US EPA.
http://www.fluorideaction.org/pesticides/tetraconazole.epa.2005.facts.pdf
-- Tetraconazole is
considered moderately toxic to birds
and highly toxic to fish, aquatic invertebrates,
algae/aquatic plants and sediment dwelling organisms.
Tetraconazole has been shown to be hazardous to bees,
when they are exposed through oral or contact means. (page 21)
-- Persistent
in water sediment.
For the most part, sediments were anaerobic, and the majority
of the radioactivity found was parent compound indicating very
little metabolism of tetraconazole under anaerobic conditions.
For the whole water/sediment systems, half-lives were calculated
as 382 and 318 days for the pond and runoff system respectively
demonstrating the persistence of tetraconazole in such systems.
(page 18-19)
-- Persistent
in soil.
The other two field studies determined tetraconazole residues
in soil samples obtained from field tests where tetraconazole
was applied as a single dose. The tests were conducted over 1
year to 67 weeks and covered 5 soil types. Both these studies
indicated very little movement of tetraconazole with no residues
being detected below 10 cm. Degradation
rates varied significantly between the soils and half lives ranged
from 0.79 weeks (5.5 days) to 69 weeks (483 days). Despite
rapid initial degradation in some of the soils, tetraconazole
was clearly persistent as over the course of the studies,
insufficient degradation occurred to allow a DT90 to be calculated
(page 19). The main concern is with persistence
and accumulation in soils and further work in this area
is recommended with any future application involving an extension
to higher rates and more frequent applications. (page 21)
-- Toxic
to fish.
Fish: Acute toxicity tests were performed on freshwater fish under
static renewal or flow through conditions. On the basis of these
results, tetraconazole is considered toxic
to fish with 96 h LC50s ranging from >2.5-4.3 mg ac/L.
Fathead minnow was tested for toxicity to their early life stages.
This test established a 34 day NOEC of 1.09 ppm and a LOEC of
3.21 ppm. An acute toxicity study was performed on each of the
metabolites SLM-2 and SLM-6 on rainbow trout. The results indicate
that metabolite SLM-6 is practically non-toxic to fish whereas
metabolite SLM-2 has a 96 h LC50 of 24 mg/L. (page 20)
-- Toxic
to very toxic to aquatic invertebrates.
Tetraconazole and formulated product were tested acutely on one
freshwater invertebrate (Daphnia) under static conditions and
one salt water species of mysid shrimp under static conditions.
The 48 h EC/LC50 values derived for daphnia and mysid shrimp were
1.8-3.0 and 0.42 mg ac/L, respectively, indicating tetraconazole
is toxic to very toxic to aquatic invertebrates. Daphnia
were further tested chronically under static renewal conditions.
The 21-d EC50 (reproduction) was estimated to be 0.73 mg/L. The
NOEC (21-d) was determined to be 0.56 ppm. An acute toxicity study
of each of the metabolites SLM-2 and SLM-6 indicates that SLM-6
is practically non-toxic to Daphnia while SLM-2 has an acute toxicity
of 48 h LC50 of 68 mg/L. A 28 day chronic toxicity study was carried
out on the larvae of the sediment dwelling organisms midge Chironomous
riparius. A 28 day LC50 of 5.3 mg/L for the emergence and development
rates indicates that tetraconazole is toxic to Chironomous riparius.
(page 20)
-- Moderately
toxic to earthworms.
Four toxicity studies on earthworms indicate that tetraconazole
was moderately toxic to earthworms with a 14 d LD50 of 71 mg/kg
and a corresponding NOEC of 32 mg/kg. (page 20)
Ref:
August
2005 - Evaluation of Tetraconazole in the product Domark 40ME
Fungicide. Australian Pesticides and Veterinary Medicines Authority.
http://www.fluorideaction.org/pesticides/tetraconazole.2005.report.australia.pdf
1,1,1,2-Tetrafluoroethane
(HFC-134a)
- Propellant, US EPA List 4B Inert - CAS No. 811-97-2
The
atmospheric lifetime of 1,1,1,2-tetrafluoroethane has been estimated
to range from 12.5 to 24 years.
1,1,1,2-Tetrafluoroethane may also undergo atmospheric removal
by wet deposition processes; however, any removed is expected
to rapidly re-volatilize to the atmosphere.
Ref: Hazardous Substances
Data Bank for 1,1,1,2-TETRAFLUOROETHANE CASRN: 811-97-2.
http://www.fluorideaction.org/pesticides/1,1,1,2-tetrafluoroe.toxnet.htm
TFM
(3-Trifluoro-Methyl-4-Nitro-Phenol) - Lampricide, Piscicide
- CAS No. 88-30-2
Abstract: Toxicity
testing with fish began early in this century, but standardized
methods have been developed only within the last three decades.
Standardized test procedures promote reproducibility of results;
healthy fish properly handled and acclimated to test conditions
are a given prerequisite. The principles of acute toxicity testing
are important in the design of chronic tests for suspected carcinogens
because certain factors influence the activity of chemicals or
contaminants. The pH of test water is a critical factor in governing
the uptake of chemicals by fish. Buffering is required so that
uniform pH in waters of different hardnesses and different pHs
in water of a given hardness are maintained.
The importance of water quality control is graphically demonstrated
by the lampricide 3-trifluoromethyl-4-nitrophenol; the toxicant
is over 50 times more toxic in water at pH 6.5 than at pH 9.5.
Results of laboratory tests on toxicity or carcinogenicity of
single compounds in a clean environment represent an oversimplification
of the real world because organisms are actually exposed to multiple
chemicals or stresses. Because the environment is a complex interaction
of physical, chemical, and biological factors that are extremely
variable and dynamic, simulation of these systems in the laboratory
is, at best, artificial; therefore, results developed must be
considered to be predictive.
Ref:
Marking LL (1984). Procedures for use of freshwater fishes in
the development of reproducible toxicological information. Natl
Cancer Inst Monogr 1984 May;65:195-9
http://www.ncbi.nlm.nih.gov:80/entrez/query.fcgi?cmd=Retrieve&db=PubMed&list_uids=6749253&dopt=Abstract
-- TFM is chemically
and biologically very stable. The compound
possesses many of the chemical features known to impart persistence
to organic compounds... TFM was converted to reduced-TFM
with a half-life of less than one week under both aerobic and
anaerobic aquatic metabolism conditions. It must be stressed that
when reduced-TFM is reported as a reaction product, degradation
has not occurred. TFM has just undergone a chemical reduction
and under appropriate conditions, reduced-TFM
may be re-oxidized to TFM... TFM is expected to remain
in solution in the lake system and persist
for long periods of time... TFM (C7 H4 F3 NO3 ; M.W. 207.11)
is chemically and biologically very stable.
An examination of its structure, i.e., aromatic, fluoro-containing,
m-substituted phenol, shows that the compound
possesses many of the chemical features known to impart persistence
to organic compounds. Its pKa is 6.07 and the effect of
pH on the toxicity appears to follow closely to the concentration
of the lipid-soluble, free phenol form of TFM. This pH sensitivity
is used to maximize effectiveness. As pH increases, toxicity,
bioaccumulation, and adsorption to sediment decrease. Aqueous
solubility of the sodium salt is 5 g/L.[P 24-25].
Ref:
Reregistration Eligibility Decision (RED) 3-Trifluoro-Methyl-4-Nitro-Phenol
and Niclosamide. US EPA, Office of Prevention, Pesticides And
Toxic Substances (7508C). Report No. EPA 738-R-99-007. November
1999.
http://www.fluoridealert.org/PESTICIDES/TFM.Red.1999.pdf
•
Note
from FAN:
The use of TFM in the Great Lakes began at the end of the 1950's.
Since that time there has been a dramatic shift from male to female
sea lampreys. A confounding factor may be that TFM was found to
be contaminated with dioxin in the early 1990s. It is unclear
to me whether dioxin influenced this alteration, or TFM alone,
or the combination of TFM and dioxin. [EC, Sept. 2003]
-- TFM treatments have
been associated with induction of hepatic mixed function oxyganase
activity and altered levels of circulating
steroids in fish and induced hepatic
vitellogenesis in primary cultures of rainbow trout hepatocytes
(Hewitt et al. 1997). As such, TFM acts as an
estradiol agonist and has a demonstrated
endocrine disrupting effect...
-- Abundance of sea lamprey peaked in several
Great Lakes before chemical control began. The sex ratio in these
peak populations were predominately males (68-71%). Following
a decade of lampricide treatments, populations of sea lampreys
showed marked declines and the sex ratios
in these populations shifted toward a predominance
of females accounting for 72% of the population (Henrich,
et al, 1979). This publication by Henrich concludes that lampricides
reduced the populations of sea lampreys in the Great Lakes and
contributed to the sequential shifting of
the sex composition from a predominance of males to a predominance
of females. There are no data to support that the endocrine
mediated effect associated with TFM is related to the observed
sex-ratio shifts among TFM-treated populations of sea lamprey
[page 23].
Ref: November 1999 US EPA's Reregistration
Eligibility Decision (RED) for 3-Trifluoro-Methyl-4-Nitro-Phenol
and Niclosamide).
http://www.fluoridealert.org/PESTICIDES/TFM.Red.1999.pdf
...
The sensitivity of mudpuppies, frog tadpoles, and adult frogs
to use of 3-trifluoromethyl-4- nitrophenol (TFM) in the Great
Lakes has been noted on many occasions. TFM has been used annually
since 1958 for the control of sea lampreys throughout the Great
Lakes. Amphibians regularly have been found dead in creeks immediately
after TFM treatment (Gilderhus and Johnson 1980, Matson 1990).
Laboratory tests have confirmed that species native to the Great
Lakes Basin, such as the grey tree frog, northern leopard frog,
and bullfrog, are sensitive to levels of TFM used for sea lamprey
control (Chandler and Marking 1975). Mudpuppy population size
decreased by a minimum of 29 per cent after a spray event in the
Grand River of Ohio (Matson 1990)...
Ref:
Conservation Priorities for the Amphibians and Reptiles of Canada.
Sept 2000 report published by World Wildlife Fund Canada and Canadian
Amphibian and Reptile Conservation Network. Prepared by David
Seburn and Carolyn Seburn.
Abstract. Since 1958,
3-(trifluoromethyl)-4-nitrophenol (TFM) has been used to control
the sea lamprey (Petromyzon marinus) in the USA-Canadian Great
Lakes Superior, Michigan, Huron and Ontario. A study was conducted
to determine the degradability of TFM under laboratory conditions
in aqueous (sediment-free) systems. No evidence
of microbial degradation of TFM was found up to 80 days. TFM may
persist for extended periods of time in the Great Lakes.
On the basis of past and present levels of usage of TFM, it was
estimated that the concentration of TFM in Lake Superior water
could approach, if TFM were a completely conservative chemical,
0.015 mug/l. This concentration was considerably less than the
concentrations found to be acutely and chronically toxic to aquatic
life. The use of TFM as a sea lamprey larvicide did not represent
a hazard to fish and other nontarget aquatic life in the Great
Lakes.
Ref: THINGVOLD DA et al. (1981). Persistence
of 3-(trifluoromethyl)-4-nitrophenol in aquatic environments.
ENVIRON SCI TECHNOL; 15 (11). 1335-1340.
Excerpts
from Technical
Report 7. April 2000. Animal Deformities or Reproduction
Problems. Prepared for the Lake Erie LaMP Preliminary
Beneficial Use Impairment Assessment. Keith A. Grasman,
Lead Author. Co-Authors: Christine A. Bishop, William
W. Bowerman, James P. Ludwig, Pamela A. Martin. http://www.epa.gov/glnpo/lakeerie/buia/lamp7.pdf
(page
13):
The sensitivity of mudpuppies, frog tadpoles and adult
frogs to TFM use in the Great Lakes has been noted (Gilderhus
and Johnson, 1980). TFM is intended to control larval
sea lamprey and has been used historically in 19 (8 in
U.S./11 in Canada) of the 842 tributaries to Lake Erie
for sea lamprey (Petromyzon marinus) control. Since 1995,
TFM has been applied in Conneaut Creek and the Grand River
in Ohio and Big Creek and Big Otter Creek in Ontario.
Only four Lake Erie tributaries (Big Creek Ontario, and
3 U.S. tributaries) are currently scheduled for future
regular treatments every 4 to 6 years.
When
TFM is used, amphibians have regularly been found dead
in creeks immediately after treatment in Lake Erie watersheds
and elsewhere in the Great Lakes
(Gilderhus and Johnson, 1980; Matson, 1990).
Laboratory tests have confirmed that species native to
the Great Lakes basin such as gray tree frog, leopard
frog, and bullfrog are sensitive to field applied rates
of TFM (Chandler and Marking, 1975). In the Grand
River, Ohio, Matson (1990) found that in the year following
TFM application (1997), mudpuppy
population size decreased by a minimum of 29% in the segment
treated. In 1999, the Grand
River was treated with TFM and dead mudpuppies were found
downstream of the application zone within twenty-fours
hours.
Because
TFM is not bioaccumulative and is only applied periodically
in closely controlled and monitored conditions, the associated
mudpuppy mortality is often perceived to be insignificant.
However, mudpuppies do not become
sexually mature until 4 to 6 years of age. Given
the past and projected future schedule for TFM applications,
there is the potential for the TFM applications to match
periods when large numbers of mudpuppy are reaching an
age when they can reproduce. In addition, TFM is generally
applied in the spring when stream flows are higher. Therefore,
TFM has the potential to kill a
portion of the existing females before they lay their
eggs in May and June. For these reasons, future study
is needed to determine the significance of the mortality
and the life stages most affected (see section
7.5).
(page
16)
• There are conflicting opinions about the significance
of non-target species sensitivity, particularly mudpuppy,
to TFM (when used for sea lamprey eradication), and its
implications for potential impairment. Therefore, the
impact of TFM on amphibian populations needs to be assessed
by monitoring populations of mudpuppies and other amphibians
pre- and postapplication. From a
reproductive standpoint, it is particularly important
to determine if TFM has greater impacts on certain age
classes and/or egg-bearing females.
|
Thiazopyr
- Herbicide - CAS No. 117718-60-2
Freshwater Fish: moderately
toxic
-- Rainbow trout: LC50 = 3.4 mg/L
-- Bluegill Sunfish: LC50 = 3.5 mg/L
-- Aquatic Invertebrate: moderately toxic Daphnia magna: LC50
= 6.1 mg/L
-- Mollusc Shell Deposition: highly toxic
Eastern Oyster: EC50 = 0.82 mg/L
-- Estuarine Invertebrate Acute Toxicity: Moderately toxic Mysid
Shrimp:LC50 = 2.0 mg/L Fish Early Life Stage Toxicity Rainbow
trout: NOEL = 0.55 mg/L MATC = 0.74 mg/L
-- Aquatic Invertebrate Life Cycle Toxicity Daphnia magna: NOEL
= 0.11 mg/L MATC = 0.16 mg/L Aquatic Plant Growth and Reproduction
Selenastrum capricornutun:EC50 = 0,043 mg/L NOEL = 0.018 mg/L
-- Thiazopyr had low toxicity to birds, mammals, honeybees, and
earthworms. It was moderately toxic to freshwater and marine fish
and Daphnia magna, with moderate to high
toxicity to marine invertebrates. Thiazopyr was highly
to very highly toxic to nontarget terrestrial
and aquatic plants, algae and diatoms.
-- Photodegradation
on soil: Thiazopyr degrades very slowly
in soil, with an extrapolated half life of 1373 days.
Ref: US EPA. Pesticide Fact Sheet.
Thiazopyr Reason for Issuance: Registration of a New Chemical
Date Issued: February 20, l997.
http://www.epa.gov/opprd001/factsheets/thiazopyr.pdf
Thidiazimin
-
Herbicide -
CAS No. 123249-43-4
Phototoxic Pesticide.
Light-dependent peroxidizing herbicides
(LDPHs). US EPA identified the organofluorine herbicides
Acifluorfen, Azafenidin, Carfentrazone-ethyl,
Flumiclorac-penty, Flumioxazin, Fluthiacet-methyl, Fomesafen,
Lactofen, Oxadiargyl, Oxadiazon, Oxyfluorfen, Sulfentrazone, Thidiazimin
as phototoxic pesticides that act
by inhibiting protoporphyringen oxidase in the heme and chlorophyll
biosynthetic pathway. [10
out of the 13 pesticides that EPA identified are organofluorines].
SEE
http://www.fluoridealert.org/pesticides/PHOTOTOXICITY.PAGE.htm
Ref:
December 11, 2001 - US EPA. Revised
Environmental Fate and Effects Division Preliminary Risk Assessment
for the Oxyfluorfen Reregistration Eligibility Decision Document
(also at:
http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxyefedchap.pdf
).
Tolylfluanid
- Fungicide - CAS No. 731-27-1
Water-sediment systems. In a study of hydrolysis, tolylfluanid
was readily hydrolyzed into DMST [dimethylaminosulfotoluidine]
under all conditions used (pH 4, 7 and 9; 20, 30 and 40°C).
The half life of tolylfluanid was calculated to be 11.7 days at
pH 4 and 29.1 hours at pH 7 at 22°C in respective sterile
buffer solutions. Tolylfluanid was so unstable at pH 9 that no
parent compound was left to be detected even in immediate analysis
of the sample making the estimation of half life impossible. Another
hydrolysis study demonstrated that tolylfluanid was hydrolyzed
into DMST, fluoride ion, chloride
ion, sulfur and carbon dioxide. DMST, on the other hand, was stable
at pH 4, 7 and 9 up to 55°C in respective sterile buffer solutions.
The half life of DMST was calculated to be > 1 year at 22°C
at pH 4, 7 and 9. (page 262)
Ref: Pesticide residues in food - 2002.
Report of the Joint Meeting of the FAO Panel of Experts on Pesticide
Residues in Food and the Environment and the WHO Core Assessment
Group on Pesticide Residues. Rome, Italy. 16- 25 September 2002.
ISBN 92-5-104858-4.
http://www.fluorideaction.org/pesticides/tolylfluanid.fao.2002.pdf
Transfluthrin
- Insecticide - CAS
No. 118712-89-3
Environmental toxicity
tests demonstrated that all products containing transfluthrin
should be classified as 'Extremely dangerous
to fish and other aquatic life', with a 48 h EC50 for Daphnia
magna of 1.7 ug1 and a 96 h LC50 for rainbow trout (Oncorhynchus
mykiss) of 0.7 ug 1.
Ref: Evaluation on: Transfluthrin Use as
a Public Hygiene Insecticide. September 1997. Prepared by: the
UK Health and Safety Executive, Biocides & Pesticides Assessment
Unit, Magdalen House, Stanley Precinct, Bootle, Merseyside L20
3QZ. Available from: Department for Environment, Food and Rural
Affairs, Pesticides Safety Directorate, Mallard House, Kings Pool,
3 Peasholme Green, York YO1 7PX. UK. Also at
http://www.pesticides.gov.uk/citizen/evaluations/165_confirm-box.htm
• Note:
This was transcribed from the copy available on the web. While
one can easily read this report on the web, the report is inaccessible,
or locked, to any attempt to copy it. Any errors are mine. EC.
Tributyltin
fluoride - Antifoulant, Fungicide, Microbiocide -
CAS No. 1983-10-4
Tributyltin
fluoride: Acute Aquatic Ecotoxicity Summaries for Tributyltin
fluoride on All Taxa Groups.
Ref: PAN Pesticides Database - Chemical
Toxicity Studies on Aquatic Organisms.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?CAS_No=1983-10-4&Rec_Id=PC34614
|
Common
Name |
Scientific
Name |
Avg Species
LC50 (ug/L) |
LC50 Std
Dev |
Avg Species
Rating |
Amphibians
|
Frog |
Rana temporaria |
30.0 |
- |
Very
Highly Toxic |
Crustaceans |
Fiddler
crab |
Uca pugilator |
800.0 |
- |
Highly
Toxic |
Fish |
Channel
catfish |
Ictalurus
punctatus |
8.15 |
3.85 |
Very
Highly Toxic |
Bluegill |
Lepomis
macrochirus |
7.35 |
3.65 |
Very
Highly Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
11.2 |
7.80 |
Very
Highly Toxic |
Shell thickening. Alzieu
et al. (1982) reported that adult oysters (Crassostrea gigas)
developed gel centres in the shell when
they were exposed to TBT fluoride at a concentration of 0.2 g/litre.
Ref: C Alziieu et al. (1982). Influence
des peintures antisalissures base d'organostanniques sur la
calcification de la coquille de l'huitre Crassostrea gigas. Rev.
Trav. Inst. Pches Marit., 45: 101-116.
Ref: Tributyltin Compounds. Environmental
Health Criteria 116. International Programme on Chemical Safety.
http://www.inchem.org/documents/ehc/ehc/ehc116.htm
Aquatic acute toxicity
values for tributyltin fluoride include a bleak fish 96-hour LC
50 of 2.3 ppb, an algae 72-hour EC50
of 9.3 ppb, and a Harpacticoid copepod 96-hour LC 50 of 0.8
ppb. EPA believes that there is sufficient evidence for
listing tributyltin fluoride on EPCRA section 313 pursuant to
EPCRA section 313(d)(2)(C) based on the available environmental
toxicity data.
Ref: USEPA/OPP. Support Document for the
Addition of Chemicals from Federal Insecticide, Fungicide, Rodenticide
Act (FIFRA) Active Ingredients to EPCRA Section 313. U. S. Environmental
Protection Agency, Washington, DC (1993). As cited by US EPA in:
Federal
Register: January 12, 1994. Part IV. 40 CFR Part 372. Addition
of Certain Chemicals; Toxic Chemical Release Reporting; Community
Right-to-Know; Proposed Rule.
Trichlorofluoromethane
(CFC
11) - Insecticide,
Fungicide, Propellant; EPA List 2 Inert - CAS
No. 75-69-4
US
EPA: Class 1 Ozone Depleting Substance. Lifetime
of Global Warming Potential: 45 years
Ref:
http://www.epa.gov/ozone/ods.html
Many gases emitted
as a result of industrial and agricultural activities can accumulate
in the earth's atmosphere and ultimately
contribute to alterations in the vertical distribution and concentrations
of stratospheric ozone. Among the most important are those
trace gases that have long residence times in the atmosphere.
This allows accumulation in the troposphere and a gradual upward
migration of the gases into the stratosphere where they contribute
to depletion of stratospheric ozone layer. The atmospheric and
chemical processes involved are extremely complex.
Trace gases of particular concern include certain long lived chlorofluorocarbons,
such as CFC-11, CFC-12, and CFC-113. Since the transport
of these gases to the stratosphere is slow, their residence times
there are long, and the removal processes are slow, any effect
on stratospheric ozone already seen is probably the result of
anthropogenic emissions of these gases several decades ago.
Those gases already in the atmosphere will continue to exert stratospheric
ozone depletion effects well into the next century. /Chlorofluorocarbons/
[WHO; Environmental Health Criteria 113: Fully Halogenated Chlorofluorocarbons
p.47 (1990)]
Ref:
Hazardous Substances Data Base for TRICHLOROFLUOROMETHANE.
http://www.fluoridealert.org/pesticides/Trichlorofluorometha.TOXNET.htm
Environmental
Contamination Concerns
A. Surface Water Volatilization from
water surfaces is expected to be an important fate process with
estimated volatilization half-lives for a model river and a model
lake being four hours and five days, respectively. Hydrolysis
is not expected to occur. Bioconcentration
in organisms is low to moderate; BCF (Bioconcentration factor:
the ratio of the chemical concentration in the organism to that
in surrounding water) is from 11-86. Biodegradation, adsorption
to sediment, and abiotic degradation are insignificant. Large
volumes of Freon may sink to the bottom and gradually bubble up
to the surface if the water is not too cold (Hazardtext, 2003B;
HSDB, 2001A; HSDB, 2001B).
B. Groundwater In general, Freons
that are spilled onto soil have the potential to leach into groundwater,
because they do not bind well to soil (Hazardtext, 2003B;
HSDB, 2001A; HSDB, 2001B). Fully halogenated
hydrocarbons such as Freons 11, 12, and 113 are very resistant
to chemical and biological degradation and are likely to be persistent
contaminants if they reach groundwater.
D. Soil
If Freon is spilled onto soil, a portion
may evaporate from the surface and the remainder will leach downward
into the soil. Mobility through the soil
is expected to be moderate based on estimated Koc values. Freon
does not bind well to soil, and leaching to groundwater is possible
(Hazardtext, Preliminary Remediation Goals for Residential
Soil (U.S. EPA, 2002, Region IX):
Freon 11 - 390 mg/kg
Freon 12 - 94 mg/kg
Freon 113 - 5600 mg/kg
E. Air
Once released to air, Freon exists solely as a gas. In the atmosphere,
fully halogenated Freons diffuse to the
troposphere, where they are very stable and can be transported
great distances. Wet deposition may result in some loss, but re-volatilization
into the atmosphere is likely. The only degradation process
is diffusion to the stratosphere, where photolytic destruction
of Freons results in depletion of stratospheric
ozone, thereby increasing the amount of ultraviolet-B (UV-B)
radiation reaching the earths surface (Hazardtext, 2003B; HSDB,
2001A; HSDB, 2001B). Preliminary Remediation Goals for Ambient
Air (U.S. EPA, 2002, Region IX):
Freon 11 - 0.73 mg/m 3
Freon 12 - 0.21 mg/m 3
Freon 113 - 31 mg/m 3
Ref:
September
24, 2003 (Revised)
- FREON [11, 12, 113].
Technical Support Document: Toxicology. Clandestine
Drug Labs/ Methamphetamine. Volume 1, Number 11. California EPA,
Office of Environmental Health Hazard Assessment (OEHHA), Department
of Toxic Substances Control.
Trichlorotrifluoromethane
(CFC
113)
- Solvent, US EPA List 2 Inert - CAS No. 76-13-1
US
EPA: Class 1 Ozone Depleting Substance. Lifetime
of Global Warming Potential: 85 years
Ref:
http://www.epa.gov/ozone/ods.html
The
stratospheric lifetime of this compound ranges between 63 and
122 years(5).
As a result of this persistence in the atmosphere(5), this vapor-phase
compound can be transported long distances and therefore, its
concn should be fairly uniform throughout the globe away from
known sources(SRC). [(1) Bidleman TF; Environ Sci Technol 22:
361-367 (1988) (2) Boublik T et al; The Vapour Pressures of Pure
Substances. 2nd Rev Ed, Amsterdam: Elsevier p. 74 (1984) (3) Horvath
AL et al; J Phys Chem Ref Data 28: 395-507 (1999) (4) Dilling
WL; pp. 154-97 in Environmental Risk Analysis for Chemicals. Conway
RA, ed. NY, NY: Van Nostrand Reinhold Co (1982) (5) Chou CC et
al; J Phys Chem 82: 1-7 (1978)]
Ref:
Hazardous Substances Data Bank for 1,1,2-TRICHLORO-1,2,2-TRIFLUOROETHANE
CASRN: 76-13-1.
http://www.fluorideaction.org/pesticides/trichlorotrifluorome.toxnet.htm
Environmental
Contamination Concerns
A. Surface Water. Bioconcentration
in organisms is low to moderate; BCF (Bioconcentration
factor: the ratio of the chemical concentration in the organism
to that in surrounding water) is from 11-86.
B. Groundwater.
In general, Freons that are spilled onto soil have the potential
to leach into groundwater, because they do not bind well
to soil (Hazardtext, 2003B; HSDB, 2001A; HSDB, 2001B). Fully halogenated
hydrocarbons such as Freons 11, 12, and 113 are very
resistant to chemical and biological degradation and are likely
to be persistent contaminants if they reach groundwater.
D. Soil. If
Freon is spilled onto soil, a portion may evaporate from the surface
and the remainder will leach downward into the soil. Mobility
through the soil is expected to be moderate based on estimated
Koc values. Freon does not bind well to
soil, and leaching to groundwater is possible (Hazardtext,
2003B; HSDB, 2001B).
E. Air. Once released to air, Freon
exists solely as a gas. In the atmosphere, fully halogenated Freons
diffuse to the troposphere, where they are very stable and can
be transported great distances. Wet deposition may result in some
loss, but re-volatilization into the atmosphere is likely. The
only degradation process is diffusion to the stratosphere, where
photolytic destruction of Freons results in depletion of stratospheric
ozone, thereby increasing the amount of ultraviolet-B (UV-B) radiation
reaching the earths surface (Hazardtext, 2003B; HSDB, 2001A;
HSDB, 2001B).
Ref:
September
24, 2003 (Revised). Released November 7, 2003)
- FREON [11, 12, 113].
Technical Support Document: Toxicology. Clandestine
Drug Labs/ Methamphetamine. Volume 1, Number 11. California EPA,
Office of Environmental Health Hazard Assessment (OEHHA), Department
of Toxic Substances Control.
Trifloxystrobin
- Fungicide - CAS No. 141517-21-7
Freshwater Fish and
Invertebrate Acute Toxicity
-- Rainbow trout 0.014 ppm (LC50) very
highly
toxic;
-- Bluegill sunfish 0.054 ppm (LC50) very
highly toxic;
-- Water flea 0.025 ppm (LC50)
very highly toxic;
Estuarine/Marine Fish and Invertebrate Acute Toxicity Under Flow-through
Condition LC50 or EC50 (ppb):
---- Sheepshead minnow 78 (ppb) very highly
toxic; ---- Mysid shrimp 8.62 (ppb) very
highly toxic;
---- Eastern oyster (shell deposition) 29.3 (ppb) very
highly toxic
Ref: US EPA Pesticide Fact Sheet. Trifloxystrobin.
Reason for Issuance: New Chemical Registration. Date Issued: September
20, 1999.
http://www.epa.gov/opprd001/factsheets/trifloxystrobin.pdf
...
Trifloxystrobin's major isomer, CGA-321113, forms at the average
rate of 80% of the applied parent, is persistent,
(half life is about 301 days), and soluble, 30.9 ppm and is also
mobile. The major degradate minimum Koc is 49, the median Koc
is 127 and is also stable to hydrolysis. The
major degradate, CGA-321113 is persistent and mobile and has a
potential to leach into groundwater. CGA-321113 has been found
in the soil profile at the 36 inch depth.
Ref: Federal Register: May 22, 2002 (Volume
67, Number 99)] [Rules and Regulations] [Page 35915-35924]. Trifloxystrobin;
Pesticide Tolerance. Final Rule.
http://www.fluorideaction.org/pesticides/trifloxystrobin.fr.may22.02.htm
-- Accumulation in
water and/or sediment: Trifloxystrobin will not accumulate.
CGA 321113 may accumulate in sediment (see DT50 above).
-- Remarks: Residue relevant for environmental monitoring
in water: Surface water trifloxystrobin Groundwater trifloxystrobin.
Member states may wish to monitor for NOA 413161 in vulnerable
groundwater situations as it could approach the 10g/l
drinking water limit for chlorinated aliphatic compounds compounds
even though it is considered not relevant.
Ref:
Review report for the active substance trifloxystrobin. Trifloxystrobin.
SANCO/4339/2000-Final. 7 April 2003. Finalised in the [European
Commission] Standing Committee on the Food Chain and Animal Health
at its meeting on 15 April 2003 in view of the inclusion of trifloxystrobin
in Annex I of Directive 91/414/EEC.
http://www.fluorideaction.org/pesticides/trifloxystrobin.eu.april.03.pdf
Triflumizole
- Fungicide - CAS
No. 68694-11-1
Abstract: Laboratory bioassays were conducted
to determine the contact honey bee
toxicity of commercial and candidate neonicotinoid insecticides.
The nitro-substituted compounds were the most toxic to the honey
bee in our laboratory studies with LD50 values of 18 ng/bee
for imidacloprid, 22 ng for clothianidin, 30 ng for
thiamethoxam, 75 ng for dinotefuran and 138 ng for nitenpyram.
The cyano-substituted neonicotinoids exhibited a much lower toxicity
with LD50 values for acetamiprid and thiacloprid of 7.1 and 14.6 g/bee,
respectively. Piperonyl butoxide, triflumizole
and propiconazole increased honey
bee toxicity of acetamiprid 6.0-, 244- and 105-fold
and thiacloprid 154-, 1,141- and 559-fold, respectively,
but had a minimal effect on imidacloprid (1.70, 1.85 and 1.52-fold,
respectively). The acetamiprid metabolites, N-demethyl acetamiprid,
6-chloro-3-pyridylmethanol and 6-chloro-nicotinic acid when applied
topically, produced no mortality at 50 g/bee. These results
suggest that P450s are an important mechanism for acetamiprid
and thiacloprid detoxification and their low toxicity to honey
bees. When honey bees were placed in cages in forced contact with
alfalfa treated with acetamiprid and the synergist, triflumizole,
in combination at their maximum recommended application rates,
no mortality was detected above that of the control.
Ref: Mechanism
for the differential toxicity of neonicotinoid insecticides in
the honey bee, Apis mellifera; by Takao Iwasa, Naoki Motoyama,
John T. Ambrose and R.M.R. Michael Roe. Crop Protection; Volume
23, Issue 5 , May 2004, Pages 371-378.
Ref:
PAN Pesticides Database - Chemical Toxicity Studies on Aquatic
Organisms.
Acute Aquatic Ecotoxicity Summaries for Triflumizole on All
Taxa Groups. http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC34923
|
|
|
|
|
Fish |
|
|
|
Bleak |
Alburnus
alburnus |
400.0 |
Highly
Toxic |
Bluegill |
Lepomis
macrochirus |
36.0 |
Very
Highly Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
445.0 |
Highly
Toxic |
Molluscs |
|
|
|
Snail |
Biomphalaria
glabrata |
10.0 |
Very
Highly Toxic |
Zooplankton |
Harpacticoid
copepod |
Nitocra
spinipes |
8.00 |
Very
Highly Toxic |
Triflumuron
- Insecticide - CAS No. 64628-44-0
Triflumuron
is very toxic to aquatic organisms. Triflumuron is toxic to bees.
Triflumuron: Fish
toxicity:
LC50 (96 hr) bluegill sunfish (Lepomis macrochirus) > 20.8
µg/L
LC50 (96 h) rainbow trout (onchorhynchus mykiss) > 24.2 µg/L
Triflumuron: Daphnia
toxicity:
EC50 (48 h) water flea (Daphnia magna) 1.6 µg/L
Triflumuron: Algal
toxicity:
Growth rate: IC50 (72 h) green algae (Desmodesmus subspicatus)
> 0.025 mg/L
Ref: August 9, 2004. Material
Safety Data Sheet for Alsystin 250 Larvicide. Bayer CropScience.
--
Triflumuron is a toxic hazard to juvenile aquatic and terrestrial
arthropods
--
Fish toxicity:
LC50: > 10 mg/L (96 h) rainbow trout
LC50: >100 mg/L (96 hours) golden orfe
Daphnia toxicity:
EC50: 0.23 mg/L (48 hours) daphnia magna.
--
Environmental fate, persistence and degradation:
Degradation of active constituent half life:
t l/2: 960 days at pH4 (22 0 C)
t l/2: 580 days at pH7 (22 0 C)
tl/2: 11 days at pH9 (22 0 C)
Ref: Material
Safety Data Sheet for Intrigue Termite Dust. Supplier:
Bayer Environmental Science A Business Group of Bayer CropScience
Pty Ltd ABN 87 000 226 022 Address: 391 - 393 Tooronga Road, East
Hawthorn Victoria 3123, Australia
http://www.fluorideaction.org/pesticides/triflumuron.msds.bayer.02.pdf
Trifluralin
- Herbicide - CAS No. 1582-09-8
Sheepshead
minnows, Cyprinodon variegatus Laeepede, exposed to 5 5 to 31
/xg/1 of the herbicide trifluralin, throughout their first 28
days of life, developed a heretofore undescribed vertebral dysplasia.
This dysplasia consisted of semisymmetrical
hypertrophy of vertebrae (three to 20 times normal), characterized
by foci of osteoblast and fibroblasts actively laying down bone
and bone precursors. Effects of the abnormal vertebral
development were dorsal vertebral growth into the neural canal,
ventral compression of renal ducts, and longitudinal fusion of
vertebrae. Fish, exposed for 51 days to 16-6 /ng/1 trifluralin
and thereafter depurated for 41 days, showed no increase in vertebral
dysplasia during depuration; however, residual spinal column damage
was evident. Serum calcium concentrations were elevated in adult
fish exposed for 4 days to 16-6 /xg/1 trifluralin. Fluorosis or
mimicry of hypervitaminosis A are considered possible mechanisms
for the osseous effect, but are not considered to be the only
possible causes. The highly predictable nature of this disorder
in experimental exposures strengthens the probability that young
flsh may serve as experimental models for determining effects
of chemicals on early vertebrate ontogeny, particularly in regard
to skeletal development.
Excerpt:
Trifluralin
(2, 6 dinitro-N, N-dipropyl-4-(trifluoromethyl) Benzamine) is
a fluorine containing, pre-emergent herbicide widely used in the
United States (Wiswesser 1976).
Continuous laboratory exposure of early
life stages of the sheepshead minnow Cyprinodon variegatus Laeepede
to relatively low concentrations of trifluralin results in marked
vertebral dysplasia...
Ref: Vertebral
dysplasia in young fish exposed to the herbicide trifluralin.
By JA COUCH, JT WINSTEAD, DJ HANSEN and LR GOODMAN.
Journal of Fish Diseases 1979, 2, 35-42.
Full report at: http://www.fluorideaction.org/pesticides/trifluralin.1979.paper.pdf
• trifluralin
has been added to the OSPAR (Convention for the Protection of
the Marine Environment of the North-East Atlantic) List of Chemicals
for Priority action in 2002 because it is considered to be a PBT
substance fulfilling the criteria for Persistence,
Bioaccumulation and Toxicity (page
3).
• 5.2 RISK TO AQUATIC ORGANISMS. Selenastrum capricornutum
is the most sensitive aquatic organism
on an acute time-scale and fathead minnow is the most sensitive
species on a chronic time-scale when tested with trifluralin and
the lead formulation. Due to the difference in Annex VI trigger
value, the risk assessment is driven by the endpoints for fish
both on an acute as long term time-scale. The resulting acute
TER-value at 1 m from a field (7.9) is below and hence breaches
the Annex VI trigger value of 100 so the risk should be considered
as high. The rapporteur Member State calculated the risk taking
into account buffer zones. This resulted in a TER-value of 110
indicating a low acute risk to fish if a bufferzone of 15 meters
is taken into account. The choice of a relevant endpoint for the
long-term risk to fish was extensively discussed during the EPCO
expert meeting (section ecotoxicology, June 2004). Trifluralin
induces vertebral lesions in several fish species, and in some
instances this effects is induced after short term exposure
(24 hours for brown trout). The meeting agreed that the risk assessment
should be based in initial PEC and on the NOEC of 0.3 ?g/L (based
on the observed vertebral lesions in the study with fathead minnow)
together with an uncertainty factor of 10 to conduct the risk
assessment. This would lead to a TER value of 0.38 when a buffer
zone of 15 m is taken into account (without detailed calculations,
a bufferzone of 50 m should lead to a TER-value of approximately
1). Consequently the risk for aquatic organisms should be regarded
as high. Therefore the risk should be further refined either by
higher tier studies or by a refinement of the exposure assessment.
Therefore, the expert meeting set the following
data requirement: notifier to submit exposure studies with different
exposure times using the fathead minnow as the most sensitive
fish species. As an alternative microcosm tests with a more realistic
exposure regime may be run (page 21-22).
..... Trifluralin and the metabolites
TR-4, TR-7 and TR-14 can be found in concentrations above 10%
of the AR in the sediment. Therefore the risk to sediment dwelling
organisms needs to be addressed. This risk assessment is available
in the addendum 3 of June 2004... (page 22).
..... Studies on bio-accumulation
in fish are available as the logPow exceeds 3 and the DT50 in
water exceeds 10. The steady state bioconcentration
factor is found to be 5674 which exceeds the Annex VI trigger
value of 100 for not readily biodegradable product ...
This BCF-value and the fact that the depuration is less than 95%
after 14 days triggers a fish full life cycle study which is available
with the sheephead minnow. The resulting NOEC from this study
is 1.3 µg/L (based on fecundity, no vertebral lesions observed)
which is higher than the NOEC which is chosen for the long term
risk assessment. As mentioned above a high
long term risk to aquatic organisms was identified for which a
data requirement is still open. Therefore, EFSA proposes that
Member States may reconsider the risk for bioaccumulation when
this long term assessment is revised, on receipt of the above
mentioned data requirement. Residues in fish were found during
the available field monitoring study (page 22-23).
• High
risks were identified for aquatic organisms, in particular the
chronic risk to fish, which require consideration of appropriate
risk mitigation measures.
Using the initial predicted environmental concentrations (PEC’s)
together with the no observed effect level (NOEC) of 0.3 ?g/L
leads to a toxicity exposure ratio (TER)-value of 0.38 when a
bufferzone of 15 metres is taken into account which is below the
Annex VI trigger value of 10 (without detailed calculations, a
bufferzone of 50 m should lead to a TER-value of approximately
1). Further data to address this risk is
needed and the risk assessment can only be concluded when the
outstanding data is evaluated (page
3)
Ref:
March 14, 2005. European Food Safety Authority: Conclusion regarding
the peer review of the pesticide risk assessment of the active
substance trifluralin. EFSA Scientific Report (2005) 28, 1-77.
http://www.fluoridealert.org/pesticides/trifluralin.eu.long.2005.pdf
Note:
Still in use in the EU as of October 2003; however the EU is currently
reconsidering its use.
"Trifluralin
1582-09-8 Banned. Low
degradability, bioaccumulative and toxic to water-living organisms.
1990."
Definition: "Banned. A substance which for health or environmental
reasons by an authority decision is either no longer approved
for any area of application, or for which an approval or registration
has been denied from the first instance."
Ref: Euopean Commission. Appendix 5. Substances
which may not be included as active ingredients in approved pesticide
products, Chapter 15, Section 2, subsection one.
http://www.kemi.se/lagar_eng/pdf/app5_8.pdf
Ref:
PAN Pesticides Database - Chemical Toxicity Studies on Aquatic
Organisms. Acute Aquatic Ecotoxicity Summaries for Trifluralin.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC35146
|
Common
Name |
Scientific
Name |
Avg Species LC50 (ug/L) |
LC50
Std Dev |
Number
of Studies |
Studies Avg Species Rating |
Amphibians |
Toad |
Bufo
bufo japonicus |
14,000 |
- |
1 |
Slightly
Toxic |
Fowler's
toad |
Bufo
woodhousei fowleri |
150.7 |
37.8 |
7 |
Highly
Toxic |
Fish |
Porgy |
Acanthopagrus
schlegeli |
56.0 |
- |
1 |
Very
Highly Toxic |
Bunni
fish |
Barbus
sharpeyi |
250.0 |
- |
1 |
Highly
Toxic |
Goldfish |
Carassius
auratus |
397.0 |
312.3 |
5 |
Highly
Toxic |
Agohaze,
goby |
Chasmichthys
dolichognathus |
120.0 |
- |
1 |
Highly
Toxic |
Pacific
herring |
Clupea
pallasi |
5.00 |
- |
1 |
Very
Highly Toxic |
Sheepshead
minnow |
Cyprinodon
variegatus |
190.0 |
- |
1 |
Highly
Toxic |
Common,
mirror, colored, carp |
Cyprinus
carpio |
391.2 |
377.1 |
5 |
Highly
Toxic |
Western
mosquitofish |
Gambusia
affinis |
9,630 |
9,893 |
5 |
Moderately
Toxic |
Green
fish |
Girella
punctata |
110.0 |
- |
1 |
Highly
Toxic |
Channel
catfish |
Ictalurus
punctatus |
800.7 |
711.2 |
10 |
Highly
Toxic |
Bluegill |
Lepomis
macrochirus |
197.4 |
233.1 |
40 |
Highly
Toxic |
Largemouth
bass |
Micropterus
salmoides |
86.2 |
19.5 |
4 |
Very
Highly Toxic |
Oriental
weatherfish |
Misgurnus
anguillicaudatus |
350.0 |
- |
1 |
Highly Toxic |
Striped
mullet |
Mugil
cephalus |
32.0 |
- |
1 |
Very
Highly Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
188.1 |
326.7 |
58 |
Highly
Toxic |
Medaka,
high-eyes |
Oryzias
latipes |
430.0 |
- |
1 |
Highly
Toxic |
Red
Sea Bream |
Pagrus
major |
23.0 |
2.16 |
3 |
Very
Highly Toxic |
Hirame,
flounder |
Paralichthys
olivaceus |
56.0 |
- |
1 |
Very
Highly Toxic |
Grunt |
Parapristipoma
trilineatum |
33.0 |
- |
1 |
Very
Highly Toxic |
Fathead
minnow |
Pimephales
promelas |
133.4 |
33.3 |
8 |
Highly
Toxic |
Harlequinfish,
red rasbora |
Rasbora
heteromorpha |
733.3 |
188.6 |
3 |
Highly
Toxic |
Jacopever |
Sebastes
schlegeli |
74.0 |
- |
1 |
Very
Highly Toxic |
Yellowtail |
Seriola
quinqueradiata |
5.00 |
- |
1 |
Very
Highly Toxic |
Walleye |
Stizostedion
vitreum vitreum |
180.0 |
- |
1 |
Highly
Toxic |
Triflusulfuron-methyl
- Herbicide -
CAS
No. 126535-15-7
Potential
Ground Water Contaminant.
Ref: PAN Pesticides Database - Chemicals
for Triflusulfuron-methyl.
http://www.pesticideinfo.org/Detail_Chemical.jsp?Rec_Id=PC34661
Triphenyltin
fluoride- Antifoulant, Algaecide, Herbicide
- CAS
No. 379-52-2
Severe marine pollutant.
Ref: Material Safety Data Sheet ACC# 99193.
Triphenyltin fluoride.
https://fscimage.fishersci.com/msds/99193.htm
Ref:
PAN Pesticides Database - Chemical Toxicity Studies on Aquatic
Organisms. Acute Aquatic Ecotoxicity Summaries
for Triphenyltin fluoride on All Taxa Groups.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC34678
|
|
|
|
|
Fish |
Bleak |
Alburnus
alburnus |
400.0 |
Highly
Toxic |
Bluegill |
Lepomis
macrochirus |
36.0 |
Very
Highly Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
445.0 |
Highly
Toxic |
Molluscs |
Snail |
Biomphalaria
glabrata |
10.0 |
Very
Highly Toxic |
Zooplankton |
Harpacticoid
copepod |
Nitocra
spinipes |
8.00 |
Very
Highly Toxic |
|