Note: This is not an exhaustive list. When time allows more information will be added.
Acifluorfen - Herbicide - CAS No. 50594-66-6
Phototoxic Pesticide.
Light-dependent peroxidizing herbicides (LDPHs).
US EPA identified the 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
).
Abstract: Photochemistry
studies can be helpful in assessing the environmental fate of
chemicals. Photochemical reactions lead to the formation of by-products
that can exhibit different toxicological properties from the original
compound. For this reason the photochemical behavior of the herbicide
acifluorfen (5-[2-chloro-4-(trifluoromethyl)phenoxy]-2-nitrobenzoic
acid) in the presence of different solvents was studied.
Photochemical reactions were carried out using a high-pressure
mercury arc and a solar simulator. Kinetic parameters and quantum
yields were determined. The identification
of photoproducts was performed by mass spectrometry and
[1H] nuclear magnetic resonance (NMR). Nitrofluorfen,hydroxy-nitrofluorfen,
2-chloro-4-(trifluoromethyl)phenol, 5-trifluoromethyl-5'-nitrodibenzofuran,
and other derivatives were identified. The photochemical reactions
were also carried out in the presence of either a singlet
or a triplet quencher, and in the presence of either a radical
initiator or a radical inhibitor. Substances used as inhibitors
of the excited levels T1 and S1 showed that photodegradation of
acifluorfen begins from a singlet state S1 through a pi,pi* transition.
The role of free radicals in the photodegradation of acifluorfen
was determined and a radical mechanism was proposed. Toxicity
tests against Daphnia magna Strauss showed that acifluorfen was
not toxic at a concentration of 0.1 mM; however,
photoproducts formed after 36 h of UV exposure of the herbicide
induced a remarkable toxicity to the test organism.
Ref: Photochemistry and photoinduced toxicity of acifluorfen,
a diphenyl-ether herbicide. Scrano L, Bufo SA, D'Auria M, Meallier
P, Behechti A, Shramm KW.
1: J Environ Qual 2002 Jan-Feb;31(1):268-74.
http://www.ncbi.nlm.nih.gov:80/entrez/query.fcgi?cmd=Retrieve&db=PubMed&list_uids=11837431&dopt=Abstract
Acifluorfen,
sodium -
Herbicide - CAS No. 62476-59-9
-- Ecological Risk:
... The Agency (USEPA) is uncertain about risks to freshwater
and estuarine animals. The acute toxicity data do not suggest
a risk concern. However, EPA does not have sufficient information
to assess chronic risk. A no observed adverse effect level could
not be determined in a chronic fish toxicity study because the
lowest dose level resulted in an effect (reduced larvae weight).
A comparison of the maximum peak concentration of acifluorfen
in water is 100 fold lower than the LC50 for rainbow trout or
bluegill sunfish. Because acifluorfen is persistent in water,
the Agency is concerned about the potential for chronic risk.
EPA is also concerned about the potential for chronic risk based
on the phototoxic mechanism of action of sodium acifluorfen.
Confirmatory data will be required to address this concern.
Ref: Overview of Sodium Acifluorfen Risk
Assessment April 4, 2002. USEPA.
http://www.fluorideaction.org/pesticides/acifluorfen.na.epa.apr.02.pdf
-- Environmental Fate:
Sodium acifluorfen is extremely water soluble, is stable to hydrolysis
and is moderately persistent to persistent
in soil and water. Aerobic soil metabolism half-lives ranged
from 30 days up to 6 months; anaerobic soil metabolism half-life
was less than 28 days. Acifluorfen is very mobile with low binding
potential. In soil (pH > 3.5), acifluorfen is predominately an
anion with little sorption in many soils. Acifluorfen binding
increases with soil organic carbon content. Soil temperature and
soil water content influence soil microbial activity and may influence
acifluorfen's degradation rate. The decarboxy derivative of acifluorfen
was the primary degradate found in solution. The amino analog
of acifluorfen (amino acifluorfen) is the major degradate under
anaerobic soil conditions. Depending upon soil type, amino acifluorfen
ranged from immobile to medium mobility. The aerobic aquatic half-life
was estimated to be 117 days.
-- In ground water, acifluorfen will be
persistent due to its stability to abiotic hydrolysis.
During runoff events, sodium acifluorfen may reach surface waters
from ground water where it would also persist for some time (unless
there is some photodegradation; <1 to 29 days half-life). Acifluorfen
would not be expected to bioaccumulate in fish because of the
low Kow value.
Ref: January 15, 2002. Preliminary Human
Health Risk Assessment. MEMORANDUM SUBJECT: SODIUM ACIFLUORFEN.
HED Chapter for the Reregistration Eligibility Decision Document.
US EPA, Office of Prevention, Pesticides and Toxic Substances.
http://www.fluorideaction.org/pesticides/acifluorfen.na.a.red.jan.02.pdf
Ammonium
bifluoride - Wood Preservative
- CAS No. 1341-49-7
Fluoride/fluorinated
substances identified in Agreement between Canada and the United
States on Great Lakes Water Quality, 1978.
Appendix
1
Hazardous Polluting Substances: Ammonium
Bifluoride * Ammonium Fluoborate * Ammonium
Fluoride * Ammonium Silicofluoride * Antimony Trifluoride
* Beryllium Fluoride * Ferric Fluoride * Hydrofluoric Acid * Lead
Fluoborate * Lead Fluoride * Sodium Bifluoride * Sodium Fluoride
* Zinc Fluoride * Zinc Silicofluoride * Zirconium Potassium Fluoride.
Appendix 2
Potential Hazardous Polluting Substances:
Aluminum Fluoride * Antimony Pentafluoride * Benfluralin * Chlorflurazole
* Cobaltous Fluoride * Stannous Fluoride
Ammonium
fluoride - Wood Preservative - CAS
No. 12125-01-8
Fluoride/fluorinated
substances identified in Agreement between Canada and the United
States on Great Lakes Water Quality, 1978.
Appendix
1
Hazardous Polluting Substances: Ammonium
Bifluoride * Ammonium Fluoborate * Ammonium
Fluoride * Ammonium Silicofluoride
* Antimony Trifluoride * Beryllium Fluoride * Ferric Fluoride
* Hydrofluoric Acid * Lead Fluoborate * Lead Fluoride * Sodium
Bifluoride * Sodium Fluoride * Zinc Fluoride * Zinc Silicofluoride
* Zirconium Potassium Fluoride.
Appendix 2
Potential Hazardous Polluting Substances:
Aluminum Fluoride * Antimony Pentafluoride * Benfluralin * Chlorflurazole
* Cobaltous Fluoride * Stannous Fluoride
Ammonium
silicofluoride - Insecticide, Miticide, Wood Preservative, US
EPA List 3 Inert -
CAS No. 16919-19-0
Fluoride/fluorinated
substances identified in Agreement between Canada and the United
States on Great Lakes Water Quality, 1978.
Appendix
1
Hazardous Polluting Substances: Ammonium
Bifluoride * Ammonium Fluoborate * Ammonium
Fluoride * Ammonium Silicofluoride
* Antimony Trifluoride * Beryllium Fluoride * Ferric Fluoride
* Hydrofluoric Acid * Lead Fluoborate * Lead Fluoride * Sodium
Bifluoride * Sodium Fluoride * Zinc Fluoride * Zinc Silicofluoride
* Zirconium Potassium Fluoride.
Appendix 2
Potential Hazardous Polluting Substances:
Aluminum Fluoride * Antimony Pentafluoride * Benfluralin * Chlorflurazole
* Cobaltous Fluoride * Stannous Fluoride
Barium
hexafluorosilicate - Insecticide
- CAS No. 17125-80-3
Banned
in Austria.
This action applies to barium compounds. All uses banned. High
persistence in the environment and bioaccumulation in the food
chain. Contamination of water and accumulation in plants occur.
Ref: Pan
Pesticides Database.
Benfluralin
(Benefin) - Herbicide - CAS
No. 1861-40-1
Fish
-- Goldfish (Carassius auratus) - Highly
Toxic
-- Sheepshead
minnow (Cyprinodon variegatus) - Highly
toxic
-- Bluegill (Lepomis
macrochirus) -- Highly
toxic to Very Highly Toxic
-- Rainbow trout,donaldson
trout (Oncorhynchus mykiss) - Highly
Toxic
-- Fathead minnow
(Pimephales promelas) -Highly
Toxic
Zooplankton
-- Opossum shrimp
(Americamysis bahia) - Very Highly
Toxic
Ref:
PAN Pesticides Database - Chemical Toxicity Studies on Aquatic
Organisms. Toxicity Studies for Benfluralin on All Organism Groups
- Toxicology studies on aquatic organisms from science journals.
http://www.pesticideinfo.org/List_AquireAll.jsp?Rec_Id=PC35043
Fluoride/fluorinated
substances identified in Agreement between Canada and the United
States on Great Lakes
Water Quality, 1978.
Appendix 1 - Hazardous Polluting Substances:
Ammonium Bifluoride * Ammonium Fluoborate * Ammonium Fluoride
* Ammonium Silicofluoride * Antimony Trifluoride * Beryllium Fluoride
* Ferric Fluoride * Hydrofluoric Acid * Lead Fluoborate * Lead
Fluoride * Sodium Bifluoride * Sodium Fluoride * Zinc Fluoride
* Zinc Silicofluoride * Zirconium Potassium Fluoride.
Appendix 2 - Potential Hazardous Polluting
Substances:
Aluminum Fluoride * Antimony Pentafluoride
* Benfluralin * Chlorflurazole * Cobaltous Fluoride * Stannous
Fluoride
Benzotrifluoride
- Insecticide - CAS No. 98-08-8
-- Experimental BCF
values of 26-54 and 31-58 suggest that benzotrifluoride
will bioconcentrate in aquatic organisms.
-- Environmental Bioconcentration: An estimated BCF value of 110
was calculated for benzotrifluoride(SRC), using an experimental
log Kow of 3.01(1) and a recommended regression-derived equation(2).
Bioconcentration factors determined from a six week study in carp
using 100 and 10 ug/L benzotrifluoride were 26-54 and 31-58, respectively(3).
According to a classification scheme(4), these
BCF values suggest that bioconcentration in aquatic organisms
will be an important fate process(SRC).
[(1) Hansch C, Leo A; The Log P Database. Claremont, CA: Pomona
College (1987) (2) Lyman WJ et al; Handbook of Chemical Property
Estimation Methods. Washington DC: Amer Chem Soc pp. 5-4, 5-10
(1990) (3) Chemicals Inspection and Testing Institute; Biodegradation
and Bioaccumulation Data of Existing Chemicals Based on the CSCL
Japan. Japan Chemical Industry Ecology - Toxicology and Information
Center. ISBN 4-89074-101-1 (1992) (4) Franke C et al; Chemosphere
29: 1501-14 (1994)]
Ref: TOXNET profile from Hazardous Substances
Data Base.
http://www.fluoridealert.org/pesticides/Benzotrifluoride.TOXNET.HSD.htm
Beta-cyfluthrin
- Insecticide - CAS No. 68359-37-5
Acute and chronic toxicity studies show that the technical material
and formulations of beta-cyfluthrin are highly
toxic to fish and aquatic invertebrates and moderately
toxic to algae. It is classified as presenting a high
risk to honey bees and other arthropod species.
Ref: 1999. FAO Specifications and Evaluations
for Plant Protection Products. Beta-Cyfluthrin (1RS, 3RS; 1RS,
3SR)-3-(2,2-dichloro-vinyl)-2,2-dimethyl-cyclopropane-carboxylic
acid (RS)-cyano
-(4-fluoro-3-phenoxy-phenyl)-methyl ester. Food and Agricultural
Organization of the United Nations.
http://www.fao.org/WAICENT/FAOINFO/AGRICULT/AGP/AGPP/Pesticid/Specs/pdf/Beta_cyf.pdf
•
Definition of arthropod:
Includes arachnids (spiders, mites) insects (bee, ant, moth)
and crustaceans (shrimp, crab), as a group under Phylum Arthropoda,
all invertebrates (no vertebral column), having segmented bodies
and hollow, jointed legs.
Honeybees.
Acute oral toxicity: LD50 ~ 0.05 µg/bee Acute contact toxicity:
LD50 ~ 0.001 µg/bee
-- Aquatic Organisms.
Acute toxicity fish:
-- LC50 = 0.068 µg/l (Oncorhynchus mykiss; 96 h);
-- §-cyfluthrin LC50 = 0.28 µg/l (Lepomis macrochirus; 96 h);
§-cyfluthrin
Long term toxicity fish:
-- NOEC = 0.01 µg/l (Oncorhynchus mykiss; 58 d; cyfluthrin)
-- NOEC = 0.14 µg/l (Pimephales promelas; 307 d; cyfluthrin)
Ref: December 2002 - Beta-cyflutrin: Review
report for the active substance beta-cyfluthrin Finalised in the
Standing Committee on the Food Chain and Animal Health at its
meeting on 3 December 2002 in view of the inclusion of beta-cyfluthrin
in Annex I of Directive 91/414/EEC. EUROPEAN COMMISSION HEALTH
& CONSUMER PROTECTION DIRECTORATE-GENERAL Directorate E Ü Food
Safety: plant health, animal health and welfare, international
questions E1 - Plant health.
http://www.fluorideaction.org/pesticides/cyfluthrin.beta.eu.dec.2002.pdf
Bifenthrin
-
Acaricide, Insecticide - CAS Numbers: 82657-04-3
Persistence
in sediment
Abstract: Pyrethroids are commonly used insecticides in both agricultural
and urban environments. Recent studies showed that surface runoff
facilitated transport of pyrethroids to surface streams, probably
by sediment movement. Sediment contamination by pyrethroids is
of concern due to their wide-spectrum aquatic toxicity. In this
study, we characterized the spatial distribution and persistence
of bifenthrin [BF; (2-methyl(1,1'-biphenyl)-3-yl)methyl
3-(2-chloro-3,3,3-trifluoro-1-propenyl)-2,2-dimethylcyclopropanecarboxylate]
and permethrin [PM; 3-(2,2-dichloroethenyl)-2,2-dimethylcyclopropanecarboxylic
acid (3-phenoxyphenyl)methyl ester] in the sediment along a 260-m
runoff path. Residues of BF and PM were
significantly enriched in the eroded sediment, and the magnitude
of enrichment was proportional to the downstream distance. At
145 m from the sedimentation pond, BF was enriched by >25 times,
while PM isomers were enriched by >3.5 times. Pesticide enrichment
along the runoff path coincided with enrichment of organic carbon
and clay fractions in the sediment, as well as increases in adsorption
coefficient K(d), suggesting that the runoff flow caused selective
transport of organic matter and chemical-rich fine particles.
Long persistence was observed for BF under both aerobic and anaerobic
conditions, and the half-life ranged from 8 to 17 mo at 20 degrees
C. The long persistence was probably caused by the strong pesticide
adsorption to the solid phase. The significant enrichment,
along with the prolonged persistence, suggests that movement of
pyrethroids to the surface water may be caused predominantly by
the chemically rich fine particles. It is therefore important
to understand the fate of sediment-borne pyrethroids and devise
mitigation strategies to reduce offsite movement of fine sediment.
Ref: Distribution and persistence of pyrethroids
in runoff sediments; by Gan
J, Lee SJ, Liu WP, Haver DL, Kabashima JN. J Environ Qual. 2005
Apr 20;34(3):836-41.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15843646&query_hl=11
Abstract: In Pakistan there is little data on environmental contamination
of rural water sources by pesticides. This study evaluated pesticide
contamination of groundwater in four intensive cotton growing
districts. Water samples were collected from 37 rural open wells
in the areas of Bahwalnagar, Muzafargarh, D.G. Khan and Rajan
Pur districts of Punjab and analysed for
eight pesticides which are mostly used. Information on
types of pesticide used and distance to nearest pesticide mixing
area and application areas was obtained for each site. From the
eight pesticides analysed, six pesticides were detected in the
water samples. Only cypermethrin and cabosulfan were not detected.
The percentage of detection of bifenthrin,
lambda-cyhalothrin, carbofuran, endosulfan, methyl parathion and
monocrotophos was, respectively 13.5%,
5.4%, 59.4%, 8%, 5.4% and 35.1% in July;
16.2%, 13.55%, 43.2%, 8%, N.D. (not
detected) and 24.3% in October. Maximum
contamination levels (MCLs) established by the U.S. Environmental
Protection Agency for drinking water were not exceeded. The study
has shown the need for monitoring pesticide contamination in rural
water resources, and the development of drinking water quality
standards for specific pesticides in Pakistan. The conclusions
and recommendations will be disseminated to senior decision makers
in central and local governments, extension agents and farmers.
Ref: Pesticides in shallow groundwater
of Bahawalnagar, Muzafargarh, D.G. Khan and Rajan Pur districts
of Punjab, Pakistan; by Tariq MI, Afzal S, Hussain I. Environ
Int. 2004 Jun;30(4):471-9.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15031006&query_hl=11
Abstract: The use of pyrethroid insecticides is increasing for
agriculture, commercial pest control, and residential consumer
use. In addition, there is a trend toward the use of newer and
more potent compounds. Little is known about the toxicity of sediment-associated
pyrethroid residues to aquatic organisms, yet recent work has
shown they commonly are found in aquatic sediments in the heavily
agricultural Central Valley of California, USA. Minimal data exist
on the sensitivity of standard sediment toxicity testing species
to pyrethroids, despite two or more decades of agricultural use
of these compounds. Sediment concentrations
causing acute toxicity and growth impairment to the amphipod Hyalella
azteca were determined for six pyrethroids in three sediments,
ranging from 1.1 to 6.5% organic carbon (OC). In order of decreasing
toxicity of sediment-associated residues, the compounds tested
were bifenthrin (average 10-d median lethal concentration [LC50]
= 0.18 microg/g OC), lambda-cyhalothrin (0.45 microg/g
OC), deltamethrin (0.79 microg/g OC), esfenvalerate (0.89 microg/g
OC), cyfluthrin (1.08 microg/g OC), and permethrin (4.87 microg/g
OC). In a sediment containing about 1% OC, most pyrethroids, except
permethrin, would be acutely toxic to H. azteca at concentrations
of 2 to 10 ng/g dry weight, a concentration only slightly above
current analytical detection limits. Growth typically was inhibited
at concentrations below the LC50; animal biomass on average was
38% below controls when exposed to pyrethroid concentrations roughly
one-third to one-half the LC50. Survival data are consistent with
current theory that exposure occurs primarily via the interstitial
water rather than the particulate phase. A
reanalysis of previously reported field data using these toxicity
data confirms that the compounds are exceeding concentrations
acutely toxic to sensitive species in many agriculture-dominated
water bodies.
Ref: Use
and toxicity of pyrethroid pesticides in the Central Valley, California,
USA. Amweg EL, Weston DP, Ureda NM. Environ Toxicol Chem. 2005
Apr;24(4):966-72.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15839572&query_hl=11
Aquatic acute toxicity
values for bifenthrin include a bluegill 96- hour LC
50 of 0.35 ppb, a rainbow trout 96-hour LC
50 of 0.15 ppb, a sheepshead minnow LC
50 of 17.5 ppb, and a daphnid 48-hour EC
50 of 1.6 ppb. EPA believes that there is sufficient evidence
for listing bifenthrin 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.
Abstract:
The acute and chronic toxic effects of bifenthrin on Daphnia magna
were studied. The results showed that 24
h-EC50, 48 h-LC50 and 96 h-LC50 of bifenthrin on D. magna were
3.24, 12.40 and 1.40 microg/L respectively. And the LOEC and NOEC
of bifenthrin were 0.02 and 0.004 microg/L respectively.
The recovery test of bifenthrin on Daphnia magna was presented.
Daphnia magna (F0 generation) were exposed during 21 d to different
bifenthrin concentrations. Offspring (animals from the first and
third brood: F1 (1st) and F1 (3rd), respectively) were transferred
to a free pesticide medium during a 21 d recovery period. In this
recovery study, survival, growth, reproduction (mean total young
per female, onset of reproduction and number broods per female)
and the intrinsic rate of natural increase (r) were assessed as
parameters. Reproduction such as number of young per female as
well as length was still reduced in F1 (1st) generation daphnids
from parentals (F0) exposed to the bifenthrin. However F, (3rd)
individuals from parentals exposed to pesticide concentrations
were able to restore reproduction when a recovery period of 21
d was allowed, but the length of F, (3rd)
from parentals exposed to the 0.5 and 0.75 microg/L bifenthrin
concentration was still significantly effected (P < 0.05).
Ref: Effects
of bifenthrin on Daphnia magna during chronic toxicity test and
the recovery test; by Ye WH, Wen YZ, Liu WP, Wang ZQ. J Environ
Sci (China). 2004;16(5):843-6.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15559825&query_hl=11
Abstract: Recent studies
showed that synthetic pyrethroids (SPs) can move via surface runoff
into aquatic systems. Fifty-six of SP-degrading bacteria strains
were isolated from contaminated sediments, of which six were evaluated
for their ability to transform bifenthrin and permethrin in the
aqueous phase and bifenthrin in the sediment phase. In the aqueous
phase, bifenthrin was rapidly degraded by strains of Stenotrophomonas
acidaminiphila, and the half-life (t1/2) was reduced from >700
h to 30 to 131 h. Permethrin isomers were degraded by Aeromonas
sobria, Erwinia carotovora, and Yersinia frederiksenii. Similar
to bifenthrin, the t1/2 of cis- and trans-permethrin was reduced
by approximately 10-fold after bacteria inoculation. However,
bifenthrin degradation by S. acidaminiphila was significantly
inhibited in the presence of sediment, and the effect was likely
caused by strong adsorption to the solid phase. Bifenthrin
t1/2 was 343 to 466 h for a field sediment, and increased to 980
to 1200 h for a creek sediment. Bifenthrin degradation in the
inoculated slurry treatments was not greatly enhanced when compared
with the noninoculated system. Therefore, although SP-degrading
bacteria may be widespread in aquatic systems, adsorption to sediment
could render SPs unavailable to the degraders, thus prolonging
their persistence.
Ref:
Microbial transformation of pyrethroid insecticides in aqueous
and sediment phases; by Lee S, Gan J, Kim JS, Kabashima JN, Crowley
DE. Environ Toxicol Chem. 2004 Jan;23(1):1-6.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=14768859&query_hl=11
Fish
-- Sheepshead minnow
(Cyprinodon variegatus) - Very Highly
Toxic
-- Gizzard shad (Dorosoma cepedianum) - Very
Highly Toxic
Ref:
Acute Aquatic Ecotoxicity Summaries for
Bifenthrin on All Taxa Groups. PAN Pesticides Database
- Chemical Toxicity Studies on Aquatic Organisms.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC32863
Fish
-- Sheepshead
minnow Cyprinodon variegatus - -
Very Highly Toxic
-- Bluegill (Lepomis macrochirus) -
Very Highly Toxic
-- Rainbow
trout,donaldson trout Oncorhynchus mykiss -
Very Highly Toxic
Ref:
PAN Pesticides Database - Chemical Toxicity Studies on Aquatic
Organisms. Toxicity Studies for Bifenthrin
on All Organism Groups - Toxicology studies on aquatic organisms
from science journals.
http://www.pesticideinfo.org/List_AquireAll.jsp?Rec_Id=PC32863
Bromethalin
- Rodenticide - CAS No. 63333-35-7
Ecological Toxicity
Data. Primary toxicity to mammals is very
high for all five of these rodenticides. Primary
toxicity to birds is high to very high for the single-feeding
compounds (brodifacoum, bromadiolone, bromethalin)...
Toxicity to aquatic organisms ranges from moderate to very high.
Ref: US
EPA Reregistration Eligibility Decision (RED) Rodenticide Cluster.
EPA738-R-98-007. July 1998
-- Bluegill sunfish
(Lepomis macrochirus) - Very highly toxic
-- Rainbow trout (Oncorhynchus mykiss) -
Very highly toxic
Ref:
Table 46 - Bromethalin Freshwater Fish Acute Toxicity (page 64)
US
EPA Reregistration Eligibility Decision (RED) Rodenticide Cluster.
EPA738-R-98-007. July 1998
Carbon
Tetrafluoride
- Former US EPA List 3 Inert
- CAS No. 75-73-0
Carbon tetrafluoride
(CF4) and carbon hexafluoride (C2F6) are emitted as by-products
of the primary aluminum production process. Both are potent
greenhouse gases, with global warming potentials of approximately
6,500 and 9,200 times that of CO2, respectively, and lifetimes
that exceed 10,000 years.
Ref: Mitigating Climate Change. US Department
of State
http://www.state.gov/www/global/oes/97climate_report/part4b.html
Carfentrazone-ethyl
-
Herbicide
- CAS No. 128639-02-1
-- Plants. In terrestrial
plant testing, the onion is the most sensitive plant with regard
to seedling emergence (EC25 0.009 lb/A a.i.) and the tomato is
the most sensitive in regard to vegetative vigor (EC25 0.0012
lb/a.i.). On the basis of the NOEL's the radish and lettuce were
most sensitive; both had vegetative vigor NOEL's of 0.0004 pounds
a.i./A. Carfentrazone-ethyl is highly toxic
to aquatic plants.
Ref: US EPA Pesticide Fact Sheet. Carfentrazone-ethyl
Reason for Issuance:New Chemical Registration Date Issued: September
30, 1998.
http://www.epa.gov/opprd001/factsheets/carfentrazone.pdf
Phototoxic Pesticide.
Light-dependent peroxidizing herbicides
(LDPHs). US
EPA identified the 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
).
Environmental aspects...
its major metabolites are mobile to very highly mobile in soil
and have potential to leach, though significant downward
leaching was not detected in field trials.
Ref:
April 2000 - Australia. Evaluation of the new active CARFENTRAZONE-ETHYL
in the product AFFINITY 400 DF HERBICIDE. National Registration
Authority for Agricultural and Veterinary Chemicals. NRA Ref.
51555.
http://www.fluorideaction.org/pesticides/carfentrazone-e.aus.2000rpt.pdf
Also available at http://www.apvma.gov.au/publications/prscar.pdf
Chlorfenapyr
-
Acaracide, Insecticide - CAS No. 122453-73-0
Environmental
Toxicity Data: Based on standard laboratory tests on this formulation
and the active ingredient chlorfenapyr, this product is
very toxic to fish, aquatic invertebrates, and honeybees, and
toxic to algae.
Ref: Pylon miticide. Material Safety Data
Sheet. February 13, 2001.
http://www.fluorideaction.org/pesticides/chlorfenapyr.msds.2001.pdf
---
Long-term exposure to chlorfenapyr leads to reduced egg production,
reduced hatching success and reduced nestling survival in the
avian species tested. The fact that these effects occur at a chlorfenapyr
doses above 0.059 mg/kg-bw/day (NOEL) active ingredient in the
diet make chlorfenapyr one of the most reproductively
toxic pesticides to avian species that EFED has evaluated.
(page 13)
-- Freshwater Fish. Acute and chronic risk quotients for freshwater
fish are listed in Table 47. The results indicate that acute high
risk, restricted use, and endangered species LOCs are exceeded
for freshwater fish for aerial applications in regions 3, 4, and
7. The chronic risk LOC is not exceeded for freshwater fish when
the 60-day EEC is employed. However, the finding that chronic
risks are not anticipated is of low confidence because of the
limited availability of chronic effects testing data in freshwater
fish, and the persistence of the compound.
(page 9)
-- Chlorfenapyr Stability in Soil
and Its Implications for Risks From Repeated Annual Use. Laboratory
aerobic soil and field dissipation studies for chlorfenapyr show
that the compound is very stable. Indeed,
chlorfenapyr’s persistence in soil from annual treatment
to annual treatment would contribute to increasing soil residues
with time. Multiple-year applications of chlorfenapyr to
cotton fields would therefore result in asymptotic increases in
soil concentrations. As discussed for multiple-year uniform applications
in the environmental fate section, the 90 percent upper bound
for aerobic soil metabolism half-life (1.4 years, approximately
the same as the 1.3 year field disipation half-life), yields a
calculated asymptotic first-order value approaching 2.5 times
the annual application amount (1.5 leftover from previous applications
plus 1.0 from the current year application). Using the average
aerobic soil half-life of 0.96 year, rather than the upper 90%
limit of 1.4 years, the asymptotic value becomes 2.0 times the
annual amount (1.0 residual plus 1.0 current). Under the assumption
of minimal incidental soil ingestion, the effects of chlorfenapyr
accumulation in soil to approximately 1.7 to 2.5 times the first
year soil residue are essentially negligible, and do not alter
the outcome of the risk assessment. However, if higher incidental
soil ingestion rates are assumed (e.g., Bier et al. (1994) suggests
soil incidental ingestion rates as high as 30% for some probing
birds), then accumulation in soil may influence
the outcome of the risk assessment to a greater extent.
In addition, if other routes of exposure were to be considered
(e.g., dermal), accumulation of chlorfenapyr from multiple years
of use would serve to increase the exposure of chlorfenapyr in
birds in any given year. (page 15)
--
Aquatic. At the time EPA requested sediment toxicity testing,
the only protocol which had been fully developed was a 10-day
acute sediment toxicity test. However, at this time EPA has developed
a provisional guideline protocol for a 28-day chronic sediment
test. Although specific criteria for requiring a chronic toxicity
test have yet to be published, one criterion will include the
persistence of the compound. Since chlorfenapyr
has been characterized as a persistent compound, EFED will
require a chronic sediment toxicity test. In the case of marine
sediment toxicity, a chronic test is clearly justified because
the LOCs appear to be exceeded by the results of the acute study
submitted by the registrant. Because of the recent development
of protocols for chronic sediment toxicity testing, EFED recommends
that any study protocols (including the selection of test species)
developed by the registrant to address these data requirements
be submitted to the Agency for approval prior to test initiation.
(page 18)
Ref: Calculating Avian and Mammalian Dietary
Exposure Levels. . US EPA.
http://www.epa.gov/opprd001/chlorfenapyr/memoeco2.pdf
According to Kelley
R. Tucker, Director of the American Bird
Conservancy's Pesticides and Birds Campaign: "Testing
and close scientific evaluation by EPA and independent scientists
clearly revealed the persistence of this pesticide and its chronic
and reproductive risks to birds," she explained. Laboratory studies
of chlorfenapyr showed declines in test birds of close to 50%
in number of eggs laid, number of viable embryos, and number of
normal hatchlings, leading EPA science staff to label chlorfenapyr
as "one of the most reproductively toxic
pesticides to avian species [the Division] has evaluated."
It was also found to persist in soils for over a year, leading
many to question its hidden, long-term effects on the environment.
Ref:
March 16, 2000, press release from the American Bird Conservancy.
"EPA Decision Prevents Pesticide Threat to Birds Successful
campaign, led by the American Bird Conservancy, halts hazardous
pesticide."
http://www.fluorideaction.org/pesticides/chlorfenapyr.abc.mar.2000.htm
Chlorfluazuron
- Insecticide -
CAS No.71422-67-8
Abstract: This study
was conducted to investigate the toxicity of aldicarb, cypermethrin,
profenofos, chlorfluazuron, atrazine,
and metalaxyl toward mature Aporrectodea caliginosa earthworms.
The effects of the LC(25) values of these pesticides on the growth
rate in relation to glucose, soluble protein, and activities of
glutamic-oxaloacetic transaminase (GOT), glutamic-pyruvic transaminase
(GPT), acid phosphatase (AcP), and alkaline phosphatase (AIP)
were also studied. The results showed that aldicarb was the most
toxic of the tested pesticides, followed in order by cypermethrin,
profenofos, chlorfluazuron, atrazine,
and metalaxyl. A reduction in growth rate
was observed in all pesticide-treated worms, which was accompanied
by a decrease in soluble protein and an increase in transaminases
and phosphatases. Relationships between growth rate, protein content,
transaminases, and phosphatases provided strong evidence for the
involvement of pesticidal contamination in the biochemical changes
in earthworms, which can be used as a bioindicator of soil contamination
by pesticides.
Ref: Environ Toxicol. 2003 Oct;18(5):338-46.
Comparative
toxicity and biochemical responses of certain pesticides to the
mature earthworm Aporrectodea caliginosa under laboratory conditions.
Mosleh YY, Ismail SM, Ahmed MT, Ahmed YM.
1-chloro-1,1-difluoroethane
- Solvent, EPA Inert List 2
- CAS No. 75-68-3
"Dangerous
for the ozone layer"
Ref:
OBSERVATION LIST: examples of substances requiring particular
attention second, revised edition, 1998. Issued by the Swedish
National Chemicals Inspectorate in collaboration with the Swedish
Environmental Protection Agency and the Swedish National Board
of Occupational Safety and Health.
http://www.fluorideaction.org/pesticides/sweden.dangerous.subs.1998.pdf
Chlorodifluoromethane
-
Insecticide, Fungicide, Propellant - CAS No. 75-45-6
"Dangerous
for the ozone layer"
Ref:
OBSERVATION LIST: examples of substances requiring particular
attention second, revised edition, 1998. Issued by the Swedish
National Chemicals Inspectorate in collaboration with the Swedish
Environmental Protection Agency and the Swedish National Board
of Occupational Safety and Health.
http://www.fluorideaction.org/pesticides/sweden.dangerous.subs.1998.pdf
Abstract: Chlorodifluoromethane
(HCFC-22), the most widely used substitute
for chlorofluorocarbons, is currently emitted into the atmosphere
at a global rate of about 220,000 tyr-1. In this work,
national emissions of HCFC-22 for the year 1990 are estimated
using the calculated emissions of CFC-12 as a surrogate distribution
function. The releases so calculated match the sp arse published
data in most cases.
Ref: Estimated national releases
to the atmosphere of chlorodifluoromethane (HCFC-22) during 1990;
by Pauline M. Midgley and Archie McCulloch. Atmospheric Environment
; Volume 31, Issue 6 , March 1997, Pages 809-811.
Clodinafop-propargyl
-
Herbicide - CAS No. 105512-06-9
-- Ecological Characteristics.
Aquatic: Clodinafop-propargyl is highly
toxic to freshwater fish and no more than moderately toxic
to freshwater invertebrates (LC50 = 0.30 ppm and EC50 > 2.0 ppm,
respectively). The primary degradate, CGA-193469, is no more than
moderately toxic to freshwater invertebrates (EC50 > 9.2 ppm).
Plants: Tier II seedling emergence tests with clodinafop-propargyl
indicate that ryegrass (shoot weight) at 0.031 lb. ai/Acre is
the most sensitive species of all monocot and dicots tested. For
Tier II vegetative vigor, corn (phytotoxicity) at 0.0048 lb. ai/Acre
is the most sensitive species of all species tested. Aquatic plant
testing with clodinafop-propargyl indicates that the vascular
plant, Lemna gibba, and the nonvascular plant, Navicula pelliculosa,
are the most sensitive species (EC50 > 2.4 ppm and 3.0 ppm, respectively).
Based on the estimated environmental concentrations (EECs) of
clodinafop-propargyl and its acid metabolite, CGA-193469, the
use of Discoverª Herbicide is not expected to pose a risk to non-target
organisms, with the exception of non-target plants.
There is a concern for endangered terrestrial plants inhabiting
dry and semi-aquatic areas adjacent to wheat fields when Discoverª
is applied by air.
-- Potential to Contaminate Drinking Water. The likelihood of
drinking water contamination by the parent compound, clodinafop-propargyl,
is low due to high sorption and rapid degradation in the environment.
However, the major degradate, CGA-193469,
is persistent and highly mobile in low and moderate organic
matter soils and has the potential to contaminate
drinking water...
Ref: US EPA Pesticide Fact Sheet. Reason
for Issuance: Conditional Registration. June 6, 2000.
http://www.epa.gov/opprd001/factsheets/clodinafop.pdf
Cloransulam-methyl
- Herbicide - CAS No. 147150-35-4
-- The structurally-similar
transformation products occur in aerobic and anaerobic metabolism
studies and appear persistent under anaerobic conditions. Cloransulam-methyl
is highly mobile while the major transformation
product also appears to be mobile in soils. Cloransulam-methyl
dissipated relatively rapidly from the upper 15 cm of bare ground
plots. Transformation products indicate that metabolism and photolysis
are likely to be major routes of transformation of cloransulam-methyl
in the field. Leaching may play an
important role in dissipation of cloransulam-methyl from the surface
layer. So while cloransulam-methyl and its transformation products
are likely to be only of slight persistence in the surface, the
chemicals may become more persistent when leached into the subsurface.
A label Groundwater Application Advisory is required and prospective
groundwater monitoring studies are a condition of registration.
-- Due to concerns about the mobility and potential persistence
of cloransulam-methyl and its structurally-similar, biologically
active transformation products in the subsurface and ground water,
and surface water the following label statements are required:
Groundwater Advisory This chemical and its transformation products
demonstrate the properties and characteristics associated with
chemical detected in ground water. The use of this chemical in
areas where soils are permeable particularly where the water table
is shallow, may result in ground-water contamination.
Surface Water Advisory This chemical can contaminate surface water
through spray drift.
-- Under some conditions, this chemical, and/or its transformation
products, may have a high
potential for runoff into surface water (primarily via dissolution
in run off water) for several weeks post-application.
Vulnerable Conditions include poorly draining or wet soils
with readily visible slopes toward adjacent surface waters, frequently
flooded area, areas over-laying extremely shallow ground water,
areas with in-field canals or ditches that drain to surface-water,
areas not separated or adjacent surface waters with vegetated
filter strips, and areas over-laying tile drainage systems that
drain to surface water.
-- Prospective groundwater monitoring studies are a condition
of registration. The Health Level in water for cloransulam-methyl
and/or its acid, cloransulam, is 1000 ppb based on an RfD of 0.1
mg/kg bw/day, and a 10 kg child consuming 1 Liter of water of
day. An Ecotoxicity Level will be determined, if necessary, upon
receipt and review of the Tier II Phytotoxicity Studies required
as a condition of registration. DowElanco agreed to exposure reductions
if residues of cloransulam-methyl occur at or above 50% of the
health level (500 ppb) in public and private wells. DowElanco
will develop modeling scenarios for each of the prospective groundwater
monitoring sites simulating conditions over a maximum of 100 years.
Ref: USEPA. Pesticide Fact sheet. Cloransulam-methyl.
Reason for Issuance: Conditional Registration Date Issued: October
29, 1997.
http://www.epa.gov/opprd001/factsheets/cloransulam.pdf
Cyfluthrin
-
Insecticide - CAS No. 68359-37-5
Aquatic
acute toxicity
values for cyfluthrin include a rainbow trout 96-hour LC
50 of 0.68 ppb, a bluegill 96-hour LC
50 of 1.5 ppb, and a daphnid 48-hour EC 50 of 0.14
ppb. EPA believes that there is sufficient evidence for
listing cyfluthrin 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.
Environmental Quality
Standards (EQSs) for the protection of saltwater life have been
proposed
(and were put into legislation in 1989) for the following chemicals
used as mothproofing agents;
PCSDs; cyfluthrin; sulcofuron; flucofuron and permethrin... toxicity
of cyfluthrin to saltwater life at
concentrations above the EQS of 0.001 mg l-1 in the water column.
Ref:
UK Marine Special Areas of Conservation. Mothproofing chemicals.
http://www.ukmarinesac.org.uk/activities/water-quality/wq8_25.htm
or http://www.fluoridealert.org/pesticides/Flucofuron.UK.Moth.water.htm
Cyhalothrin
- Acaracide, Insecticide - CAS
No. 68085-85-8
Highly
toxic to fish, aquatic invertebrates and honeybees.
"Cyhalothrin and lambda-cyhalothrin are very toxic
to fish in clean water under laboratory conditions. The available
data, summarized in Table 6, demonstrate a similar high acute
toxicity for both cold and warm water species of fish... Cyhalothrin
and lambda-cyhalothrin have been shown to be toxic
to honey-bees (Apis mellifera) in laboratory tests (Table
10)."
Ref: ENVIRONMENTAL HEALTH CRITERIA 99: International
Programme on Chemical Safety
http://www.inchem.org/documents/ehc/ehc/ehc99.htm#SubSectionNumber:6.2.2
Cyhalothrin,
lambda -
Insecticide - CAS No. 91465-08-6
WHO/IPCS evaluated
lambda-cyhalothrin and classified it as "Moderately Hazardous"
(Class II), on the basis of acute oral toxicity data (WHO 1999).
The hazards and risks were summarized as follows: harmful; irritating
to eyes, skin and upper respiratory system; ingestion could lead
to neurological symptoms such as tremors and convulsions; a hazard
of ingested liquid formulations is aspiration of the solvent into
the lungs (chemical pneumonitis); very toxic
to fish and honey bees.
... Lambda-cyhalothrin
is highly toxic to fish, aquatic arthropods and honey-bees
but WHO concluded that recommended use rates would not lead to
levels presenting environmental hazards.
Ref: 1999. FAO Specifications and Evaluations
for Plant Protection products. Lambda-Cyhalothrin.
Food and Agricultural Organization of the United Nations.
http://www.fao.org/WAICENT/FAOINFO/AGRICULT/AGP/AGPP/Pesticid/Specs/pdf/Lam_cyha.pdf
Highly
toxic to fish and aquatic invertebrates.
"Cyhalothrin and lambda-cyhalothrin are very toxic to fish
in clean water under laboratory conditions. The available data,
summarized in Table 6, demonstrate a similar high acute toxicity
for both cold and warm water species of fish... Cyhalothrin and
lambda-cyhalothrin have been shown to be toxic to honey-bees (Apis
mellifera) in laboratory tests (Table 10)."
Ref: ENVIRONMENTAL HEALTH CRITERIA 99: International
Programme on Chemical Safety
http://www.inchem.org/documents/ehc/ehc/ehc99.htm#SubSectionNumber:6.2.2
Abstract: In Pakistan there is little data on
environmental contamination of rural water sources by pesticides.
This study evaluated pesticide contamination of groundwater in
four intensive cotton growing districts. Water samples were collected
from 37 rural open wells in the areas of Bahwalnagar, Muzafargarh,
D.G. Khan and Rajan Pur districts of Punjab and analysed
for eight pesticides which are mostly used. Information
on types of pesticide used and distance to nearest pesticide mixing
area and application areas was obtained for each site. From the
eight pesticides analysed, six pesticides were detected in the
water samples. Only cypermethrin and cabosulfan were not detected.
The percentage of detection of bifenthrin,
lambda-cyhalothrin, carbofuran, endosulfan,
methyl parathion and monocrotophos was, respectively 13.5%,
5.4%, 59.4%, 8%, 5.4% and 35.1%
in July; 16.2%,
13.55%, 43.2%, 8%, N.D. (not detected)
and 24.3% in October. Maximum contamination
levels (MCLs) established by the U.S. Environmental Protection
Agency for drinking water were not exceeded. The study has shown
the need for monitoring pesticide contamination in rural water
resources, and the development of drinking water quality standards
for specific pesticides in Pakistan. The conclusions and recommendations
will be disseminated to senior decision makers in central and
local governments, extension agents and farmers.
Ref: Pesticides in shallow groundwater
of Bahawalnagar, Muzafargarh, D.G. Khan and Rajan Pur districts
of Punjab, Pakistan; by Tariq MI, Afzal S, Hussain I. Environ
Int. 2004 Jun;30(4):471-9.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15031006&query_hl=11
Abstract: The rainbow trout fish cell lines RTG-2
and RTL-W1 were used to determine the cytotoxic effects of the pesticides
bifenthrin, cypermethrin, cyhalothrin,
lambda-cyhalothrin, quinalphos and
chlorpyrifos. Cytotoxicity was measured by EROD and beta-Gal enzymatic
activities, the neutral red (NR) uptake assay, and the FRAME KB
protein (KBP) assay. The beta-Gal activity was unaffected by the
pesticide exposure. The EROD activity was
induced by cyhalothrin and lambda-cyhalothrin (RTG-2 and RTL-W1)
and by bifenthrin (RTL-W1). Dose dependent inhibition responses
were observed for EROD activity in cells exposed to quinalphos (RTL-W1)
and chlorpyrifos (RTG-2 and RTL-W1). RTL-W1 offered a better response
for EROD induction. The EC50 values on EROD endpoint were more sensitive
than NR and KBP. The acute fish toxicity of chlorpyrifos and quinalphos
depends highly on the species; the species sensitivity distributions
cover several orders of magnitude and the values obtained for EROS
were within the lowest part of the reported ranges.
Ref: In vitro toxicity of selected
pesticides on RTG-2 and RTL-W1 fish cell lines; by Babin MM, Tarazona
JV. Environ Pollut. 2005 May;135(2):267-74.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15734586&query_hl=11
Abstract: The use of pyrethroid insecticides is increasing for
agriculture, commercial pest control, and residential consumer
use. In addition, there is a trend toward the use of newer and
more potent compounds. Little is known about the toxicity of sediment-associated
pyrethroid residues to aquatic organisms, yet recent work has
shown they commonly are found in aquatic sediments in the heavily
agricultural Central Valley of California, USA. Minimal data exist
on the sensitivity of standard sediment toxicity testing species
to pyrethroids, despite two or more decades of agricultural use
of these compounds. Sediment concentrations
causing acute toxicity and growth impairment to the amphipod Hyalella
azteca were determined for six pyrethroids in three sediments,
ranging from 1.1 to 6.5% organic carbon (OC). In order of decreasing
toxicity of sediment-associated residues, the compounds tested
were bifenthrin (average 10-d median lethal
concentration [LC50] = 0.18 microg/g OC), lambda-cyhalothrin
(0.45 microg/g OC), deltamethrin (0.79 microg/g OC), esfenvalerate
(0.89 microg/g OC), cyfluthrin (1.08 microg/g OC), and permethrin
(4.87 microg/g OC). In a sediment containing about 1% OC, most
pyrethroids, except permethrin, would be acutely toxic to H. azteca
at concentrations of 2 to 10 ng/g dry weight, a concentration
only slightly above current analytical detection limits. Growth
typically was inhibited at concentrations below the LC50; animal
biomass on average was 38% below controls when exposed to pyrethroid
concentrations roughly one-third to one-half the LC50. Survival
data are consistent with current theory that exposure occurs primarily
via the interstitial water rather than the particulate phase.
A reanalysis of previously reported field
data using these toxicity data confirms that the compounds are
exceeding concentrations acutely toxic to sensitive species in
many agriculture-dominated water bodies.
Ref: Use and toxicity of pyrethroid pesticides
in the Central Valley, California, USA; by Amweg EL, Weston DP,
Ureda NM. Environ Toxicol Chem. 2005 Apr;24(4):966-72.
http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?cmd=Retrieve&db=pubmed&dopt=Abstract&list_uids=15839572&query_hl=11
Dichlofluanid
- Fungicide, Acaricide, Wood Preservative - CAS No.1085-98-9
Very high toxicity to aquatic organisms.
Ref: Examples
of substances requiring particular attention. Swedish
National Chemicals Inspectorate in collaboration with the Swedish
Environmental Protection Agency and the Swedish National Board
of Occupational Safety and Health. NATIONAL CHEMICALS INSPECTORATE.
Order No 510 622. Second, revised edition, 1998.
Dichlofluanid
is toxic to the freshwater algae Scenedesmus subspicatus
which had 96 h EbC50 and ErC50 values of > 1 mg l -1 ; this
was the highest concentration tested. Dichlofluanid
is toxic to Daphnia magna, with an acute study resulting
in a 48 h EC50 value of 0.42 mg ai l -1 and a NOEC of 0.07 mg
l -1 . In a chronic study, Daphnia reproduction was inhibited
by 51.7 % at 0.2 mg ai l -1 . Acute toxicity studies on the rainbow
trout and blue gill sunfish resulted in 96 h LC50 values of 0.010
and 0.030 mg ai l -1 respectively, with NOECs of < 0.024 and
< 0.0026 mg l -1 for bluegill sunfish and rainbow trout respectively.
A study investigating the effects of dichlofluanid on carp resulted
in a NOEC of 0.05 mg l -1 ... Although no
marine data were submitted, dichlofluanid was shown to be highly
toxic to aquatic organisms. The species
most sensitive to chronic effects was Daphnia magna, with a 24
- d NOEC (reduced reproduction) of 40 µg ai l -1 .
Ref:
January 2003 - Evaluation
on: Booster biocides in antifouling products. Full review of Dichlofluanid.
No. 206. Evaluation of Fully Approved or Provisionally Approved
Products. Prepared by : The 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.
Organic booster biocides
were recently introduced as alternatives to organotin compounds
in antifouling products, after restrictions imposed on the use
of tributyltin (TBT) in 1987. Replacement
products are generally based on copper metal oxides and
organic biocides. This ban has led to an increase in alternative
coating products containing the above biocides.
The most commonly used biocides in antifouling paints are:
Irgarol 1051, diuron, Sea-nine 211, dichlofluanid,
chlorothalonil, zinc pyrithione, TCMS (2,3,3,6-tetrachloro-4-methylsulfonyl)
pyridine, TCMTB [2-(thiocyanomethylthio) benzothiazole], and zineb.
Since 1993, several studies have demonstrated
the presence of these biocides in European coastal environment
as a result of their increased use. More recently, the presence
of these biocides was also revealed in waters from Japan, United
States, Singapore, Australia and Bermuda. This paper reviews
the currently available data on the occurrence of these biocides
in the aquatic environment. Some data dealing with the environmental
fate, partitioning, behaviour and risk assessment of antifouling
paint booster biocides are also reported in order to discuss the
detected levels of contamination.
Ref:
Worldwide occurrence and effects of antifouling paint booster
biocides in the aquatic environment: a review. I.
K. Konstantinou, and T. A. Albanis. Environment International;
Volume 30, Issue 2 , April 2004, Pages 235-248.
Dichlorodifluoromethane -
(CFC 12) - Insecticide, Fungicide, Propellant; EPA List 2 Inert
- CAS No. 75-71-8
US
EPA: Class 1 Ozone-Depleting Substance. Lifetime of Global Warming
Potential: 100 years
Ref:
http://www.epa.gov/ozone/ods.html
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, 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 earthÕs 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.
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: Dichlorodifluoromethane. TOXNET profile
from Hazardous Substances Data Bank.
http://www.fluorideaction.org/pesticides/dichlorodifluorometh.toxnet.htm
-- The realization
that certain chlorofluorocarbons can accumulate in the upper atmosphere
and deplete the earth's ozone layer has had a major impact on
chemicals like dichlorodifluoromethane which are used in large
quantities and have the stability to reach the stratosphere. Uses
such as propellants in aerosols which had accounted for about
75% of the release of dichlorodifluoromethane and trichlorofluoromethane,
the chemicals of greatest concern (refrigerants and foams accounted
for about 14 and 12%, respectively), were banned in the US after
Dec 15, 1978(1). Previously dichlorodifluoromethane was the principal
propellant for non-food aerosols(1) and 60% of dichlorodifluoromethane
and trichlorofluoromethane production went into aerosols(1). [(1)
Smart BE; Kirk Othmer's Encycl Chem Tech 3rd NY,NY: Wiley Interscience
10: 829-70 (1980)]
Ref:
Dichlorodifluoromethane. TOXNET profile from Hazardous Substances
Data Bank.
http://www.fluorideaction.org/pesticides/dichlorodifluorometh.toxnet.htm
Dichlorofluoromethane (CFC-21) - Propellant, EPA List
2 Inert - CAS No. 75-43-4
US
EPA: Class II Ozone-Depleting Substance. All the class II substances
and their isomers are regulated under the accelerated phaseout.
Ref:
http://www.epa.gov/ozone/ods2.html
Hydrochlorofluorocarbons
are known to release chlorine radicals into the stratosphere.
Chlorine radicals act as catalysts to reduce
the net amount of stratospheric ozone.Stratospheric ozone
shields the earth from ultraviolet-B (UV-B) radiation (i.e., 290
to 320 nanometers). Decreases in total column ozone will increase
the percentage of UV-B radiation, especially at its most harmful
wavelengths, reaching the earth's surface...Exposure to UV-B radiation
has been implicated by laboratory and epidemiologic studies as
a cause of two types of nonmelanoma skin cancers: squamous cell
cancer and basal cell cancer. Studies predict that for every 1
percent increase in UV-B radiation, nonmelanoma skin cancer cases
would increase by about 1 to 3 percent... Because this increased
UV-B radiation can be reasonably anticipated
to lead to cancer and other chronic human health effects and significant
adverse environmental effects, EPA believes there is sufficient
evidence for listing the following HCFCs [Dichlorofluoromethane
was included] that are commercially viable on EPCRA section
313 pursuant to EPCRA sections 313(d)(2)(B) and (C). EPA is proposing
that the following HCFCs be added individually to EPCRA section
313:
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.
Dichlorotetrafluoroethane
(CFC-114)
- Propellant;
Former EPA List 2 Inert - CAS No. 76-14-2
US
EPA: Class 1 Ozone-Depleting Substance. Lifetime of Global Warming
Potential: 300 years
Ref:
http://www.epa.gov/ozone/ods.html
Hydrochlorofluorocarbons
are known to release chlorine radicals into the stratosphere.
Chlorine radicals act as catalysts to reduce
the net amount of stratospheric ozone.Stratospheric ozone
shields the earth from ultraviolet-B (UV-B) radiation (i.e., 290
to 320 nanometers). Decreases in total column ozone will increase
the percentage of UV-B radiation, especially at its most harmful
wavelengths, reaching the earth's surface...Exposure to UV-B radiation
has been implicated by laboratory and epidemiologic studies as
a cause of two types of nonmelanoma skin cancers: squamous cell
cancer and basal cell cancer. Studies predict that for every 1
percent increase in UV-B radiation, nonmelanoma skin cancer cases
would increase by about 1 to 3 percent... Because this increased
UV-B radiation can be reasonably anticipated
to lead to cancer and other chronic human health effects and significant
adverse environmental effects, EPA believes there is sufficient
evidence for listing the following HCFCs [Dichlorofluoromethane
was included] that are commercially viable on EPCRA
section 313 pursuant to EPCRA sections 313(d)(2)(B) and (C). EPA
is proposing that the following HCFCs be added individually to
EPCRA section 313:
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.
Diflovidazin
- Acaricide, Insecticide - CAS No. 162320-67-4
Diflubenzuron
-
Chemosterilant, Insecticide - CAS No. 35367-38-5
Measured
aquatic acute toxicity data for diflubenzuron include a
48-hour LC 50 of 4.55 ppb for daphnids.
EPA believes that there is sufficient evidence for listing diflubenzuron
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.
Diflufenican
- Herbicide - CAS No. 83164-33-4
-- Risk to mammals.
Since new environmental fate and behaviour data have reported
that diflufenican persists in the soil,
there may be an increased risk of secondary poisoning to small
mammals feeding on contaminated earthworms. Therefore, the risk
of secondary poisoning to small earthworm eating mammals will
be addressed using the available mammalian toxicity data.
... highly persistent in the soil with dissipation
DT50 values of 311 to 733 days, as
well as in the water body with little hydrolysis over a
range of pH levels at 22C. This could lead to prolonged contamination
of water due to run-off of soil containing residues and through
direct contamination of water by overspray or spray drift (page
43).
Ref: September
1995. Evaluation
on Diflufenican. Evaluation of fully approved or provisionally
approved products. Department for Environment, Food and Rural
Affairs, Pesticides Safety Directorate, Mallard House, Kings Pool,
3 Peasholme Green, York YO1 7PX, UK.
http://www.pesticides.gov.uk/citizen/evaluations/evallist_alphabet.htm
Diflufenzopyr
- Herbicide - CAS No. 109293-97-2
A metabolite of diflufenzopyr known as
M9: 8-methylpyrido[2,3-d]pyridazine-2,5(1H,
6H)-dione
• Results of biotransformation studies using a loam
soil under aerobic conditions indicate that diflufenzopyr
will be non persistent, and transformation product M9
will be persistent (page 33)
• Results of biotransformation studies in a
flooded sandy loam soil with pond water under anaerobic conditions
indicate that diflufenzopyr is expected to be slightly
persistent under anaerobic aquatic conditions. Of the two major
transformation products that were formed, M1 was transient and
M9 has potential for persistence in water
and sediment under anaerobic conditions. (page 33)
• For biotic transformation in the
terrestrial environment, diflufenzopyr was not persistent
under aerobic soil conditions and
transformation product M9 was persistent
(page 37)
• For biotic transformation in the
aquatic environment, diflufenzopyr was slightly persistent
under aerobic aquatic conditions
(McEwan and Stephenson 1979). Major transient transformation products
M1 and M9 were detected at a maximum of 16% of the applied adioactivity,
and were not expected to persist in the aquatic environment. Under
anaerobic aquatic conditions, diflufenzopyr was slightly persistent
(McEwan and Stephenson 1979). Of the two major transformation
products that were formed, M1 was transient and M9
persisted in water. (page 38)
Ref: March 4, 2005 - DISTINCT.
Proposed Regulatory Decision Document PRDD2005-01. Pest Management
Regulatory Agency. Ottawa, Canada. The herbicide Distinct contains
20% diflufenzopyr (109293-97-2) and 50% dicamba
Dimefox
-
Acaracide, Insecticide - CAS
No. 115-26-4
Toxic
to bees. [Hartley,
D. and H. Kidd (eds.). The Agrochemicals Handbook. Old Woking,
Surrey, United Kingdom: Royal Society of Chemistry/Unwin Brothers
Ltd., 1983.,p. A150/OCT 83]
Ref:
Dimefox: TOXNET profile from Hazardous Substances Data Base.
http://www.fluorideaction.org/pesticides/dimefox.toxnet.hsdb.htm
Dinitramine
- Herbicide - CAS
No. 29091-05-2
|
|
|
Fish |
Common,
mirror, colored, carp |
Cyprinus
carpio |
Moderately
Toxic |
Northern
pike |
Esox
lucius |
Highly
Toxic |
Channel
catfish |
Ictalurus
punctatus |
Moderately
Toxic |
Bluegill |
Lepomis
macrochirus |
Moderately
Toxic |
Coho
salmon,silver salmon |
Oncorhynchus
kisutch |
Moderately
Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
Highly
Toxic |
Yellow
perch |
Perca
flavescens |
Highly
Toxic |
Fathead
minnow |
Pimephales
promelas |
Moderately
Toxic |
Brown
trout |
Salmo
trutta |
Moderately
Toxic |
Lake trout,
siscowet |
Salvelinus
namaycush |
Moderately
Toxic |
Ref:
Dinitramine: from Pesticide Action Network, http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=29091-05-2&Rec_Id=PC33330&Taxa_Group=Fish |
Dithiopyr
- Herbicide - CAS
No.
97886-45-8
|
|
|
Fish |
Sheepshead
minnow |
Cyprinodon
variegatus |
Moderately
Toxic |
Bluegill |
Lepomis
macrochirus |
Highly
Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
Highly
Toxic |
Zooplankton |
Opossum
shrimp |
Americamysis
bahia |
Highly
Toxic |
Ref:
Dithiopyr. Acute
Aquatic Ecotoxicity Summaries for Dithiopyr on All Taxa Groups.
PAN Pesticides Database - Chemical Toxicity Studies on Aquatic
Organisms. http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC33292
|
Epoxiconazole
-
Fungicide - CAS No. 135319-73-2 (formerly
106325-08-0)
"Epoxyconazole
106325-08-0 Banned. Low degradability, toxic
to water-living organisms and endocrine effects. 1997."
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
Ethalfluralin
- Herbicide
-
CAS No. 55283-68-6
Ecological
Effects
-- ... Technical ethalfluralin is highly
to very highly toxic to rainbow trout and bluegill sunfish.
The formulated product also is highly toxic to bluegill sunfish.
Since ethalfluralin persists in soils and
is very highly toxic to fish, an acute toxicity sediment
study was submitted. This study shows that ethalfluralin released
from soil sediments can be lethal to sunfish when concentrations
in water reach 17 to 58 parts per billion (ppb). In an early life
stage toxicity test with freshwater fish, ethalfluralin
affected larval length and weight in trout. In invertebrate
toxicity studies, technical ethalfluralin is very highly toxic
and the formulated product is slightly toxic to Daphnia magna
on an acute basis. In a life cycle study using daphnids, reproduction
was the most sensitive parameter affected. Ethalfluralin
is highly toxic to marine/estuarine fish, mollusks, and shrimp
on an acute basis...
Ecological Effects Risk Assessment
-- ... Ground applications of ethalfluralin could result in potential
risks to aquatic organisms from runoff and drift. Although neither
high acute risk nor chronic risk to aquatic organisms is anticipated,
the restricted use trigger has been exceeded for freshwater organisms,
and endangered species triggers are exceeded for freshwater organisms
and estuarine/marine invertebrates.
-- Endangered species levels of concern
are exceeded for freshwater organisms and estuarine/marine invertebrates
from unincorporated applications; for freshwater fish from incorporated
applications; and for plants growing in wet areas receiving channelized
runoff from treated sites (from unincorporated applications).
Limitations may be imposed on the use of ethalfluralin to protect
threatened and endangered species when EPA implements the Endangered
Species Protection Program, later in 1995.
Ref: US EPA. Reregistration Eligibility
Decision (RED): Ethalfluralin. March 1995.
http://www.fluorideaction.org/pesticides/ethalfluralin.red.long.pdf
Etoxazole
- Miticide, Ovicide - CAS No.
153233-91-1
Ecological Characteristics/Risk...
etoxazole is considered very highly toxic
to aquatic invertebrates in acute testing. Acute toxicity
tests of etoxazole with freshwater fish are considered invalid for
reasons including solubility problems and failure to use flow-through
test methods, among others. Additional studies are required to characterize
acute toxicity on freshwater fish. As with avian risk, however,
significant exposure to aquatic, non-target organisms is not expected
to occur. Therefore, chronic testing is not required.
Ref: US EPA Pesticide
Fact Sheet. August 2002.
http://www.epa.gov/opprd001/factsheets/etoxazole.pdf
|