Note:
This is not an exhaustive list.
When time allows more information will be added.
Hexaflumuron
- Insecticide, Plant Growth Regulator - CAS No. 86479-06-3
Hexaflumuron
is
very toxic to aquatic animals;
concentrations of 0.1 parts per billion kill water fleas (US EPA.
Office of Pesticide Programs. 1994. Pesticide fact sheet: Hexaflumuron.
Washington, D.C. (Mar. 10)). It is persistent
in soil, with a half-life (the time required for breakdown
of half the amount applied) between 100 and 160 days (Yon, D.
et al. 1992. The environmental distribution of hexaflumuron. Brighton
Crop Protection Conference-Pests and diseases-1992: 902-912.)
Ref: Subterranean Termites. Part 2, by Caroline
Cox. Journal of Pesticide Reform / Summer 1997. Vol. 17, No. 2
http://www.pesticide.org/subtermites2.pdf
-- Environmental Bioconcentration:
An estimated BCF of 4,700 was calculated for hexaflumuron(SRC),
using a log Kow of 5.68(1) and a regression-derived equation(2).
According to a classification scheme(3),
this BCF suggests the potential for bioconcentration in aquatic
organisms is very high(SRC). [(1) Tomlin CDS, ed; The Pesticide
Manual World Compendium. 11th ed, Surrey, England: British Crop
Protection Council, p. 676 (1997) (2) Meylan WM et al; Environ
Toxicol Chem 18: 664-72 (1999) (3) Franke C et al; Chemosphere
29: 1501-14 (1994)]
-- LD50
Bee oral & contact >0.1 mg/bee
[Tomlin, C.D.S. (ed.). The Pesticide Manual - World Compendium.
10th ed. Surrey, UK: The British Crop Protection Council, 1994.
564]
Ref: Hazardous Substances Data Bank for
HEXAFLUMURON CASRN: 86479-06-3 (online October 9, 2003). Available
at Toxnet.
Hexaflurate
-
Herbicide, Wood Preservative - CAS
No. 17029-22-0
Very
toxic to aquatic organisms, may cause long-term adverse effects
in the aquatic environment.
Ref: Potassium hexafluoroarsenate(V). ChemExper Chemical Directory.
http://www.chemexper.com/chemicals/supplier/cas/17029-22-0.html
Abstract: Studies were
conducted to determine how herbicides applied at various rates
and by various methods, other than dusting, might affect honey
bees. Some herbicides appeared relatively nontoxic. Others, such
as picloram, may be beneficial. Herbicides
which were highly toxic when fed or sprayed on colonies were
paraquat, MAA, MSMA, DSMA, hexaflurate,
and cacodylic acid. Diesel oil and a phytobland oil, used as carriers,
were toxic the first day they were sprayed on bees. Although the
phenoxy herbicides (2,4,-D, 2,4,5-T, silvex, etc.) were relatively
non-toxic to adults, they stopped brood rearing and prevented
eggs from hatching when high concentrations were fed to colonies
in sugar syrup or water. Soon after this feeding was stopped,
the colonies returned to normal. Surfactants drowned large numbers
of bees for as long as six months after they were placed in a
water supply. Residues of 2,4,5-T were found in honey
bees, honey, and wax in small and perhaps unimportant amounts
for more than one year. Aerial spraying of 2,4-D, 2,4,5-T, and
a cotton desiccant did not cause any noticeable loss of honey
bees when colonies were located in the sprayed area. The results
of this study indicate that some factors which influence the losses
of honey bees include the rate of application, the herbicide used,
the method and time of application, the sources of water available,
the plants to which the herbicide is applied, and the location
of nectar, pollen, and water sources for the bees. It is concluded
that the greatest danger lies in the use of oils high concentrations
of DSMA, MSMA, paraquat, and similar chemicals which are employed
to kill all vegetation to which they are applied. This is done
frequently to control plants along and in irrigation ditches,
and along rights-of-way for railroads and highways.
Ref: Moffett JO et al. (1975).
How herbicides affect honey bees. Am. Bee J. 115(5): 178-179,
200.
Hydramethylnon
- Insecticide - CAS No. 67485-29-4
The
96-hour LC 50 in the Chanel Catfish was 90
ppb. Bioaccumulation factors in
bluegill sunfish are 1300 for the
whole fish, 780 for the fillet, and
1900 for viscera. EPA believes that
there is sufficient evidence for listing hydramethylon on EPCRA
section 313 pursuant to EPCRA section 313(d)(2)(C) based on the
available environmental toxicity data and the potential for bioaccumulation.
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
Hydramethylon
Table 9: Freshwater Fish Acute Toxicity
Ref:
US EPA. Reregistration Eligibility Decision (RED) Hydramethylnon.
EPA 738-R-98-023. December 1998. http://www.fluoridealert.org/pesticides/Hydramethylnon.RED.1998.pdf |
Species/
(Flow-through or Static) |
% ai
|
96-hour
LC50 (ppm)* |
Toxicity
Category |
MRID |
Study
Classification |
Rainbow
trout (Oncorhynchus mykiss) |
92% |
0.15 |
Highly
toxic |
00052857
|
Acceptable |
Bluegill
sunfish (Lepomis macrochirus) |
92% |
1.7 |
Moderately |
00061708
|
Acceptable |
Channel
catfish (Ictalurus punctatus) |
92% |
0.09 |
Very
highly toxic |
00061707 |
Acceptable |
Hydramethylnon.
Ref: Acute Aquatic Ecotoxicity Summaries for Hydramethylnon
on All Taxa Groups. PAN Pesticides Database - Chemical Toxicity
Studies on Aquatic Organisms. http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC33088 |
|
|
|
|
|
|
Fish |
Channel
catfish |
Ictalurus
punctatus |
96.7 |
24.9 |
3 |
Very
Highly Toxic |
Bluegill |
Lepomis
macrochirus |
910.0 |
790.0 |
2 |
Highly
Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
128.7 |
37.5 |
3 |
Highly
Toxic |
Fathead
minnow |
Pimephales
promelas |
157.5 |
82.5 |
2 |
Highly
Toxic |
Indoxacarb
- Insecticide - CAS No. 173584-44-6
-- Toxicity to Aquatic
Animals - Indoxacarb, its R-enantiomer and
degradates are "moderately to very highly toxic" to
freshwater and estuarine/marine fish on an acute basis with LC50
s ranging from 0.024 to > 1.3 mg/L. These same compounds
are "moderately toxic" to "very
highly toxic" freshwater and estuarine/marine invertebrates
on an acute basis with EC50 s ranging from 0.029 to 2.94 mg/L.
Chronic toxicities range from 0.0006 to 0.0184 mg/L for estuarine
fish and invertebrates and from 0.004 to 0.15 mg/L for freshwater
fish and invertebrates.
-- Aquatic Organisms - The acute restricted use level of concern
(0.1) was only marginally exceeded for for one scenario (estuarine/marine
invertebrates) for indoxacarb, its R-enantiomer and one degradate
(JT333).
-- Birds - The acute restricted risk levels of concern (0.1) were
only marginally exceeded for two avian scenarios and one avian
food item (short grass) as a result of multiple applications of
indoxacarb and it R-enantiomer.
-- Mammals - Several subchronic/chronic levels of concern for
small mammals (1.0) were exceeded for several food items; however,
these risks are based on conservative assumptions (potentially
reversible hemolytic effects) and the importance of these toxic
effects on survival of wildlife is uncertain.
-- Bees - Risks to bees via the dietary
route were considered minimal; however, high
toxicities were noted by the contact routes.
-- Endangered Species - The level of concerns for endangered species
(0.05) were only marginally exceeded for one scenario (estuarine/marine
invertebrates) for indoxacarb, its R-enantiomer and one degradate
(JT333). The level of concerns for endangered species were exceed
for two avian scenarios and one avian food item as a result of
multiple applications of indoxacarb and its R-enantiomer. The
risk quotients (RQs) are likely fall below the levels of concern
upon refinement.
Ref: US EPA. Pesticide Fact Sheet. Indoxacarb
Reason for Issuance: Conditional Registration Date Issued: October
30, 2000.
http://www.epa.gov/opprd001/factsheets/indoxacarb.pdf
Isoxaflutole
- Herbicide - CAS No. 141112-29-0
-- The data available
at this time indicate that isoxaflutole is
very phytotoxic.
-- Isoxaflutole is persistent and mobile,
and may leach and accumulate in groundwater and through surface
water.
-- Potential to Contaminate Groundwater.
Isoxaflutole is mobile and is expected to
persist and accumulate in surface water and groundwater. Modeling
data show that parent isoxaflutole and its primary metabolite
RPA 202248 may accumulate to concentrations that would result
in harm to non-target plants. IsoxaflutoleÕs terminal metabolite
RPA 203328 is expected to persist and accumulate, but does not
demonstrate phytotoxicity. Additional studies, including prospective
groundwater studies and surface water monitoring, will be conducted
to determine whether isoxaflutole and its primary metabolite RPA
202248 do or do not exceed concentrations deemed potentially harmful
to the environment.
-- Aquatic - Freshwater. Isoxaflutole is moderately
toxic to the rainbow trout (96-hour LC50 > 1.7 ppm) and
to the bluegill sunfish (96-hour LC50 > 4.5 ppm). It is also moderately
toxic to Daphnia magna (48-hour EC50 > 1.5 ppm).
-- Aquatic - Estuarine/Marine. Isoxaflutole is
highly toxic to the mysid shrimp (96-hour LC50 /EC50 =
0.018 ppm) and moderately toxic to the eastern oyster (96-hour
LC50 /EC50 = 3.3 ppm). It is moderately toxic to the sheepshead
minnow (96-hour LC50 > 6.4 ppm)
-- Plants. Isoxaflutole is highly toxic
terrestrial plants (EC25 = 1 X 10 -5 pounds active ingredient./Acre).
Due to the low vapor pressure of this herbicide, and due to the
fact that it is only to be applied using ground equipment, risk
to nontarget plant species is not expected from the parent compound.
The primary metabolite RPA 202248, however, is mobile and is expected
to move off-site. Additional studies, including prospective groundwater
studies and surface water monitoring, will be conducted to determine
whether isoxaflutole and its primary metabolite RPA 202248 do
or do not exceed concentrations deemed potentially harmful to
the environment.
Ref: US EPA. Pesticide Fact Sheet. Isoxaflutole
Reason for Issuance: Conditional Registration Date Issued: September
15, 1998.
http://www.epa.gov/opprd001/factsheets/isoxaflutole.pdf
Lactofen
- Herbicide - CAS No. 77501-63-4
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
).
Lithium
perfluorooctane sulfonate
(LPOS) - Insecticide, Adjuvant - CAS
No. 29457-72-5
-- PFOS
is persistent, bioaccumulative and toxic to mammalian species...
PFOS
is persistent in the environment and has been shown to bioconcentrate
in fish. It has been detected in a number of species of wildlife,
including marine mammals. Its persistence, presence in the environment
and bioaccumulation potential indicate cause for concern.
It appears to be of low to moderate toxicity to aquatic organisms
but there is evidence of high acute toxicity to honey bees. No
information is available on effects on soil- and sediment-dwelling
organisms and the equilibrium partitioning method may not be suitable
for predicting PNECs for these compartments. PFOS has been detected
in sediment downstream of a production site and in effluents and
sludge from sewage treatment plants.
Ref:
November 21, 2002 report:
Hazard Assessment of Perfluorooctane sulfonate (PFOS) and its
salts.
Organisation for Economic Co-operation and Development. ENV/JM/RD(2002)17/FINAL.
http://www.fluorideaction.org/pesticides/pfos.final.report.nov.2002.pdf
-- The proposed use
pattern for LPOS poses minimal to no aquatic or terrestrial animal
exposure. Therefore, a risk assessment was not performed.. The
end-use bait product may be attractive to honey bees. However,
honeybee exposure is expected to be minimal because the bait unit
contains a pad which soaks up the chemical material and makes
it available to wasps and hornets, but not bees. (Wasps have sponge-like
mouthparts for lapping up liquid food, but bees have an elongated
tonguelike structure for sucking up liquid food). The
proposed label cautions that the product is highly toxic to honey
bees, and baits should be placed in areas away from flowers
to mitigate attraction and exposure. EPA found the labeling precaution
to be adequate.
-- Acceptable acute oral toxicity studies were submitted to establish
the toxicity of LPOS to birds. Results are tabulated below. Species
LD50 Toxicity Category Northern bobwhite quail (Colinus virginianus)
42 (mg/kg) - highly toxic. Mallard duck (Anas platyrhynchos) 81(mg/kg)
moderately toxic. Since one of the LD50 values falls in the range
of 10 - 50 mg/kg, LPOS is categorized as
highly toxic to avian species on an acute oral basis.
-- Two acceptable subacute dietary studies
were submitted to establish the toxicity of LPOS to birds. The
preferred test species are mallard duck and bobwhite quail. Results
of these tests are tabulated below. Species 5-Day LC50 (ppm) Toxicity
Category Northern bobwhite quail (Colinus virginianus) 220
(ppm) - highly toxic. Mallard
duck (Anas platyrhynchos) 324 (ppm)
- highly toxic. Since the LC50 falls in
the range of 51 - 500 ppm, lithium perfluorooctane sulfonate is
categorized as highly toxic to avian species on a subacute
dietary basis.
-- Insects Since its intended use is to
control related hymenopterons (wasps, hornets and yellow jackets)
there is a potential for honey bee exposure. A honey bee acute
contact study is not available for LPOS. However, results of efficacy
testing on a hornet, Dolichovespula maculata, show a that a mean
concentration of 1.5 ug per bee resulted in 93% mortality within
29 hours. These results indicate that LPOS is categorized as very
highly toxic to bees on an acute contact basis. A
honey bee acute contact study is not required, since the results
of the efficacy test have been deemed adequate to demonstrate
toxicity to honey bees.
Ref: US EPA. New Pesticide Fact Sheet. Lithium
perfluorooctane sulfonate (LPOs). August 1999.
http://www.epa.gov/opprd001/factsheets/lithium.pdf
The substance shows
moderate acute toxicity to aquatic organisms, the lowest LC50
for fish is a 96-hour LC50 of 4.7 mg/l to the fathead minnow Pimephales
promelas for the lithium salt.
Ref:
November 21, 2002 report:
Hazard Assessment of Perfluorooctane sulfonate (PFOS) and its
salts.
Organisation for Economic Co-operation and Development. ENV/JM/RD(2002)17/FINAL.
http://www.fluorideaction.org/pesticides/pfos.final.report.nov.2002.pdf
Mefluidide
and its potassium and diethanolamine salts - Herbicide,
Plant growth regulator - CAS Nos. 53780-34-0,
53780-36-2, 83601-83-6)
Based on the review of the environmental fate
data, mefluidide is moderately persistent
and mobile in terrestrial environments. Possible routes
of dissipation for mefluidide are photodegradation on soil surfaces,
microbial mediated degradation, leaching, and runoff. There are
no aerobic aquatic metabolism data to assess the environmental
fate of mefluidide in aquatic environments.
-- This screening-level (Level I) risk assessment focused on the
use of mefluidide-K, mefluidide-DEA, and mefluidide on ornamental
and turf areas. Results suggest that levels
of mefluidide in the environment, when compared with measured
toxicity for the most sensitive organisms of selected taxa, are
likely to result in direct risks to listed and non-listed species
from several different taxa. Indirect risks are also identified
for listed and non-listed non-target organisms.
-- This screening level risk assessment
shows that use of mefluidide is below the Agency’s level
of concern for direct acute (listed and non-listed) and chronic
toxic exposure to aquatic freshwater and estuarine marine organisms
and acute aquatic plants. In contrast, the
use of mefluidide is above the Agency’s level of concern
for direct acute (listed and nonlisted) and chronic toxic exposure
to mammals, birds and acute (listed and nonlisted) exposure to
terrestrial and semi aquatic plants.
-- The results of this risk assessment suggest that the
patterns of mefluidide use are such that they coincide in time
and space to areas frequented by avian and mammalian wildlife.
These areas have been demonstrated as use by wildlife as sources
of food and cover. The potentially problematic wildlife food items
suggested by this risk assessment are likely to be present in
and around the treated areas. In addition, there is potential
for indirect effects to all taxonomic groups due to changes in
habitat caused by vegetation changes. Some
uses of mefluidide may not pose a threat for avian and mammalian
wildlife, such as industrial sites that are not
frequented by wildlife
• Mammalian Acute Listed LOCs were exceeded for 15
g and 35 g mammals exposed to application rates for mefluidide-DEA
and mefluidide-K (1.0 lb ae/A at 3 applications) consuming short
grass, broadleaf plants, or small insects and 1000 g mammals that
consume short grass.
• Mammalian Acute Listed LOCs were exceeded for the LD50s/sq-ft
for 15g and 35 g mammals based on one granular application of
mefluidide at 0.5 lbs ae/acre.
• Mammalian Acute Restricted Use LOCs were exceeded for
15 g and 35 g mammals that consume short grass exposed to application
rates for mefluidide-DEA and mefluidide-K ( 1.0 lb ae/A at 3 applications).
• Mammalian Acute Restricted Use LOCs were exceeded for
the LD50s/sq-ft for small and medium-sized mammals based on one
granular application of mefluidide at 0.5lbs ae/acre.
• Mammalian Chronic LOCs (dose-based) were exceeded for
15 g mammals that consume short grass exposed to application rates
for mefluidide-DEA and mefluidide-K (1.0 lb ae/A at 3 applications)
• Avian Acute Listed LOCs were exceeded for 20 g birds that
consume short grass, tall grass and broadleaf plants and small
insects and 100 g birds that consume short grass for the 1.0 lb
ae/A modeled scenario. Non-definitive toxicity endpoints do not
allow for calculations of definitive RQs, however the ratio of
non- definitive endpoints (EECs) in this case results in acute
RQs ranging from <0.0 to <0.25.
• Avian Acute Listed LOCs were exceeded for the LD50s/sq-ft
for 20 g birds based on one granular application of mefluidide
at 0.5 lbs ae/acre.
• Avian Acute Restricted Use LOCs were exceeded for 20 g
birds that consume short grass for the 1.0 lba ae/A application
rate modeled scenario. Non-definitive toxicity endpoints do not
allow for calculations of definitive RQs, however the ratio of
non- definitive endpoints (EECs) in this case results in acute
RQs of < 0.25.
• Avian Acute Restricted Use LOCs were exceeded for the
LD50s/sq-ft for 20 g birds based on one granular application of
mefluidide at 0.5 lbs ae/acre.
• Avian Chronic LOCs (dietary-based) exceedances occurred
for birds for the 1.0 lb ae/A modeled scenario. Non-definitive
toxicity endpoints do not allow for calculations of definitive
RQs, however the ratio of non- definitive endpoints (EECs) in
this case results in acute RQs ranging from 2.9 to 6.32.
• Terrestrial and Semi-aquatic Plants (Listed Species and
Non-Listed Species) LOCs were exceeded for monocots and dicots
with the 1.0 lb ae/A spray applications of mefluidide-K and mefluidide-DEA.
LOCs were exceeded for dicots and monocots (granular applications)
with 0.5 lb ae/acre of mefluidide. Dicots demonstrated more sensitivity
than monocots in all application scenarios.
Reference: USEPA.
Re-registration Eligibility Document Environmental Fate and Effects
Science Chapter. June 9, 2007.
http://www.fluoridealert.org/pesticides/docket/EPA-HQ-OPP-2007-0431-0017.pdf
Mipafox
- Acaricide, Insecticide
- CAS No. 371-86-8
Environmental Abiotic
Degradation: ...DECOMP SLOWLY IN WATER (HALF
LIFE 200 DAYS @ PH 6)... [Spencer, E.Y. Guide to the Chemicals
Used in Crop Protection. 6th ed. Publication 1093, Research Institute,
Agriculture Canada, Ottawa, Canada: Information Canada, 1973.
357]
Ref: TOXNET profile for Mipafox from Hazardous
Substances Data Base.
http://toxnet.nlm.nih.gov/cgi-bin/sis/htmlgen?HSDB
Norflurazon
- Herbicide - CAS No. 27314-13-2
Drinking
water exposure to pesticides can occur through surface and/or
ground water contamination. The Agency considers acute (one day)
and chronic (lifetime) drinking water risks and uses either modeling
or actual monitoring data, if available, to estimate these risks.
Modeling is carried out in tiers of further refinement, and is
designed to provide a high end estimate of exposure. Norflurazon
is resistant to abiotic hydrolysis and has a relatively low volatilization
potential. Norflurazon is relatively resistant to microbial degradation
with aerobic and anaerobic half lives of 130 day (aerobic soil
metabolism study), 6-8 months (aerobic aquatic metabolism study),
and an 8 month (anaerobic aquatic metabolism study). The primary
microbial degradate is desmethyl norflurazon.
The relatively low soil/water partitioning of norflurazon indicates
that norflurazon can leach to ground water and runoff will generally
be via dissolution rather than absorption to eroding soil. The
drinking water residues of concern are norflurazon and desmethyl
norflurazon. Norflurazon has been detected in ground water in
Florida and North Carolina. According to the 1995 EFGWB
Science Chapter, parent norflurazon was detected in groundwater
Polk County, Florida at concentrations up to 64 ppb for both acute
and chronic. In a monitoring study in North Carolina, norflurazon
was detected in groundwater in concentrations ranging from 1.5
-5.3 ppb. There have been reports of norflurazon detected in groundwater
in non-target studies in several states. Although these non-target
monitoring studies do not link pesticide application to the monitoring
data, it is difficult to determine the accuracy of the results.
Two new prospective groundwater (PGW) studies were conducted in
Georgia and Florida to estimate environmental concentration (EEC)
in groundwater for parent norflurazon and desmethyl norflurazon.
PGW studies are targeted monitoring studies that link to known
use areas and application rates in evaluating the potential for
leaching to groundwater. The groundwater EEC for norflurazon is
based on concentrations from the PGW studies of 29.9 ppb for norflurazon
and 23.8 ppb for desmethyl norflurazon. The groundwater EECs are
53.7 ppb for acute exposure and 15 ppb for chronic exposure. These
groundwater EECs are less than the AgencyÕs Drinking Water Levels
of Concern (DWLOC) for both acute and chronic dietary risk. There
is limited surface water monitoring information available from
USGS studies, but the monitoring was not from targeted use areas
and parent compound only was measured in some of the studies.
Therefore, the available monitoring data is not sufficient for
a drinking water assessment. EECs were calculated using Tier II
modeling tools (PRZM-EXAMS/IR) for norflurazon and the Tier I
modeling tool (FIRST) for desmethyl norflurazon. Total estimated
residues were summed from the two models giving a peak value of
633 ppb for acute exposures and a one in ten year annual average
concentration of 185 ppb for chronic exposures. The surface water
EEC is less than the DWLOC for acute dietary risk. However,
the surface water EEC for chronic dietary risk slightly exceeds
the DWLOC for infants and children 1-12...
While the surface water EEC apparently slightly exceeds the chronic
DWLOC for infant and children sub-populations, this apparent exceedance
is not considered to be a concern based on conservative assumptions
used in modeling the chronic EECs.
Ref: US EPA May 31, 2002. Tolerance Reassessment
Progress and Risk Management Decision.
http://www.fluoridealert.org/pesticides/Norflurazon.TRED.May31.2002.pdf
Novaluron
- Insecticide - CAS No. 116714-46-6
PAGE 30: ...Novaluron is
bioaccumulative. The n-octanol–water partition coefficient
(log Kow) is 4.3, which is below the TSMP Track-1 cut-off criterion
of $5.0. However, studies have determined that the bioconcentration
factor (BCF) is between 14220x and 14645x that of the concentration
in water, which is greater than the TSMP Track-1 cut-off criterion
of BCF ≥ 5000. PAGE 4: Novaluron presents
high risks to freshwater and marine aquatic invertebrates, and
moderate risk to marine mollusks. There is also some risk
to susceptible non-target plant species. Beneficial insects, such
as, predatory mites, parasitoid wasps, and honeybees may be temporarily
suppressed. Therefore, hazard statements and specific instructions
to reduce spray drift to terrestrial insects are provided on the
product label. Depending on the type of application equipment,
timing of spray, and crop, the buffer zones may vary from 3 to
80 metres for freshwater/estuarine aquatic organisms, and 1 to
30 metres for non-target terrestrial plant species.Ref:
Proposed Registration Decision. PRD2006-05. Health Canada Pest
Management Regulatory Agency. December 22, 2006.
http://www.fluorideaction.org/pesticides/novaluron.canada.12-22-06.pdf
Noviflumuron - Insecticide - CAS No. 121451-02-3
The
data indicate that noviflumuron is relatively non-toxic
to vertebrate animals, birds, moderately toxic to fish
and highly toxic to freshwater invertebrates.
The proposed label does bear precautionary statements
regarding the high toxicity to freshwater invertebrates.
The environmental fate data indicates noviflumuron is
strongly bound to soil and has low water solubility indicating
a low potential for soil leaching. The proposed use for
noviflumuron as a self contained bait to control termites
around structures, fence posts, utility poles and landscape
plantings is not expected to pose a treat to wildlife.
Ref: 2003. Noviflumuron.
California Department of Pesticide Regulation. Public
Report 2003-5.
http://www.fluorideaction.org/pesticides/noviflumuron.ca.epa.2003.pdf
Oxyfluorfen
- Herbicide - CAS No. 42874-03-3
Highly
toxic to fish.
Ref: PAN Summary of Acute Toxicity for Organism
Group
http://www.pesticideinfo.org/PCW/Detail_Chemical.jsp?Rec_Id=PC33601
The
estimated chronic MATC values for fish and
daphnids are 9 ppb and 20 ppb oxyfluorfen, respectively.
The estimated log Kow is 6.1. EPA believes that there is sufficient
evidence for listing oxyfluorfen on EPCRA section 313 pursuant
to EPCRA section 313(d)(2)(C) based on the environmental toxicity
data and potential for bioaccumulation 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.
Also see EPA on enviro ! J Environ Sci Health Part A Tox Hazard
Subst Environ Eng 2002;37(4):521-7
--
Phototoxicity. Oxyfluorfen may pose risks to animals not conveyed
by standard guideline toxicity studies because oxyfluorfenÕs mode
of action suggests it may be more toxic in the presence of light
(phototoxic). Oxyfluorfen, and other light-dependent peroxidizing
herbicides, act in plants by producing phototoxic compounds. Toxicity
studies with oxyfluorfen and other similar herbicides suggest
the same phototoxic compounds may occur in animals as a result
of herbicide exposure. Because guideline toxicity studies are
normally conducted under relatively low, artificial light conditions,
the effects of being exposed simultaneously to oxyfluorfen and
sunlight are not known. To provide information on the magnitude
of this effect, EFED is currently requesting fish phototoxicity
studies be conducted for light-dependent peroxidizing herbicides
(Appendix D).
-- Phototoxicity is a concern for terrestrial organisms as well.
Although oxyfluorfen inhibits heme synthesis, the anemia described
in all but one of the mammalian sub-chronic studies was generally
mild, with varying hematologic abnormalities. The anemia described
one subchronic study with rats (MRID 449331-01) was more severe.
The red blood cell count was normal, but the red blood cell mass
was decreased because of the small size of the red blood cells,
presumably because of inhibition of the protoporphyrinogen oxidase
enzyme. In wild mammal populations, these
hematologic effects have the potential to magnify since the lack
of natural sunlight in the laboratory does reduce the likelihood
of activating the phototoxic effects of oxyfluorfen.
-- US EPA identified the herbicides Acifluorfen,
Azafenidin, Carfentrazone-ethyl, Flumiclorac-penty, Flumioxazin,
Fluthiacet-methyl, Fomesafen, Lactofen, Oxadiargyl, Oxadiazon,
Oxyfluorfen, Sulfentrazone,
Thidiazimin as phototoxic
pesticides [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
).
Phototoxicity:
Oxyfluorfen and other herbicidal inhibitors of protoporphyrinogen
oxidase are being evaluated by EFED and ORD for
possible phototoxicity based on reports of porphyrin accumulation
in test animals.Since the biosynthesis of heme is inhibited
by oxyfluorfen, there is the possibility
that porphyrin precursors of heme could accumulate in the skin
and be activated by light and cause toxicity. There have
so far been no indications that oxyfluorfen does cause phototoxicity.
Ref: August 8,2001. OXYFLUORFEN. Toxicology
Chapter for RED. Submission No.S549936. P.C.Code:111601. Tox.Chem.No.188AAA.
US EPA.
http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxytoxchapter.pdf
-- Risks to Terrestrial
Organisms. The results of the risk assessment do not suggest concern
for acute risks to birds or mammals. Sub-chronic
and chronic risks to terrestrial birds and mammals present a serious
concern. These toxic effects may be manifested as reproductive,
developmental, and hemolytic consequences. The
chronic LOC was exceeded for birds in all crop scenarios and for
mammals in scenarios with the highest application rate (2 lbs
ai/application). In the bobwhite quail reproduction study, reduced
chick weights were observed, which would reduce fitness if experienced
in the wild. In the 2-generation rat reproduction study,
toxic effects in adults were mortality, decreased body weight,
and liver and kidney histopathology, and toxic effects observed
in the pups were decreased body weight and a decreased number
of live pups/litter. In three of the four developmental toxicity
studies, increases in spontaneous abortions, fetal resorptions,
and fetal bone deformities as well
as decreases in litter size were observed. Any of these effects
would have an effect on the fitness of individuals, and may have
an effect on the overall fitness of wild mammal populations exposed
to oxyfluorfen.
Ref: December 11, 2001. Environmental Fate
and Effects DivisionÕs Preliminary Risk Assessment for the Reregistration
Eligibility Document for Oxyfluorfen
http://www.fluoridealert.org/pesticides/Oxyfluorfen.EnvEffects.2001.pdf
Abstract: The alterations
of the AChE activity in the brains of two fresh water fishes;
Oreochromis niloticus and Gambusia affinis were measured after
exposure to acute, sub-acute and chronic concentrations from the
widely used herbicide; oxyfluorfen. Bioassays were conducted
under controlled laboratory conditions. The used concentrations
were acute: LC50 for 6 days, sub-acute 1/3 LC50 for 15 days and
chronic 1/10 LC50 for 30 days. The obtained results showed marked
inhibitory effects of the herbicide on the activity of AChE in
both fishes. However, these effects were more pronounced
in O. niloticus where the decline in the enzyme activity ranged
from 19.7 to 81.28% while in case of G. affinis it ranged from
5.7 to 36.7%. These findings demonstrate that G. affinis is most
tolerant to oxyfluorfen toxicity compared with O. niloticus.
Ref: Toxicological effects of the herbicide
oxyfluorfen on acetylcholinesterase in two fish species: Oreochromis
niloticus and Gambusia affinis; by HM Hassanein. J Environ Sci
Health Part A Tox Hazard Subst Environ Eng 2002;37(4):521-7.
http://www.ncbi.nlm.nih.gov:80/entrez/query.fcgi?cmd=Retrieve&db=PubMed&list_uids=12046652&dopt=Abstract
Abstract: This paper
deals with the expression of the biomarker hsp70 in the liver
and kidney of the freshwater fish Oreochromis niloticus following
exposure to the herbicide oxyfluorfen (Goal). Fishes were exposed
to three concentrations, the 96-h LC50 (3 mg/L), the 96-h (1/2)LC50
(1.5 mg/L), and the 96-h (1/4)LC50 (0.75 mg/L) of oxyfluorfen
for 6, 15, and 24 days, respectively, and samples were taken at
three different time periods for each concentration. The livers
responded to the herbicide by an induction of the expression of
both the constitutive (hsp75; Mr 75 kDa) and the inducible (hsp73;
Mr 73 kDa) hsp70 proteins. In kidney, the herbicide induced a
time-dependent increase in the expression of the constitutive
hsp70 (hsp75) as well, but the inducible hsp70 (hsp73) required
much longer incubation periods to reach maximal levels (15 and
24 days). Our results suggest that expression
of hsp70 in fish is a sensitive indicator of cellular responses
to herbicide exposure in the aquatic environment.
Ref: Induction of hsp70 by the herbicide
oxyfluorfen (Goal) in the Egyptian Nile fish, Oreochromis niloticus;
by HM Hassanein et al. Arch Environ Contam Toxicol 1999 Jul;37(1):78-84.
http://www.ncbi.nlm.nih.gov:80/entrez/query.fcgi?cmd=Retrieve&db=PubMed&list_uids=10341045&dopt=Abstract
-- Risks
to Terrestrial Organisms. The results of the risk assessment
do not suggest concern for acute risks to birds or mammals. Sub-chronic
and chronic risks to terrestrial birds and mammals present a serious
concern. These toxic effects may be manifested as reproductive,
developmental, and hemolytic consequences. The chronic LOC was
exceeded for birds in all crop scenarios and for mammals in scenarios
with the highest application rate (2 lbs ai/application). In the
bobwhite quail reproduction study, reduced chick weights were
observed, which would reduce fitness if experienced in the wild.
In the 2-generation rat reproduction study, toxic effects in adults
were mortality, decreased body weight, and liver and kidney histopathology,
and toxic effects observed in the pups were decreased body weight
and a decreased number of live pups/litter. In
three of the four developmental toxicity studies, increases
in spontaneous abortions, fetal resorptions, and fetal bone deformities
as well as decreases in litter size were observed. Any
of these effects would have an effect on the fitness of individuals,
and may have an effect on the overall fitness of wild mammal populations
exposed to oxyfluorfen.
Ref: December 11, 2001. Environmental Fate
and Effects DivisionÕs Preliminary Risk Assessment for the Reregistration
Eligibility Document for Oxyfluorfen
http://www.fluoridealert.org/pesticides/Oxyfluorfen.EnvEffects.2001.pdf
(Page 39): Penosxulam is stable to hydrolysis,
and is expected to be somewhat persistent in non-aquatic environments.
The major route of dissipation for penoxsulam in clear and shallow
surface water under favorable light conditions is through direct
acqueous photolysis (t 1/2=1.5-14 days). Penoxsulam
is slightly more persistent in aerobic aquatic (t 1/2 = 12-38
days) and anaerobic environments
(t 1/2 = 34-118 days). Penoxsulam is also very mobile
(Kd=0.13-1.96), and does have the potential
to leach to ground water. The low vapor pressure and
Henry's Law constant, limits the potential of penoxsulam to
volatilization from soil and water. Eleven
major degradation products have been identified for penoxsulam.
Data are not available to fully characterize these degradates
and their respective degradation pathways.
Six of these degradation products have been identified by HED
as being of toxicological concern. These toxic residues are:
BSTCA
2-animo TCA
5-OH-penoxsulam
SFA
sulfonamide
5,8-di-OH-penoxsulam
Ref: June 18, 2007 - Penoxsulam.
Human Health Risk Assessment for Proposed Uses on Fish and Shellfish.
Docket: EPA-HQ-OPP-2006-0076-0004. USEPA.
http://www.fluorideaction.org/pesticides/EPA-HQ-OPP-2006-0076-0004.pdf
Perfluidone
- Herbicide - CAS
No. 37924-13-3
-- Adsorption and
leaching in basic soil types: Perfluidone
will leach through wet, neutral or slightly alkaline soils,
with a tendency toward greater leaching in soils having low
clay and organic matter. Leaching occurs to a lesser
extent in acidic soil.
-- Perfluidone is slightly toxic to freshwater fish species.
Studies regarding freshwater invertebrates are not acceptable,
and there are no marine/estuarine data. A detailed ecological
hazard assessment cannot be made until certain environmental
chemistry data requirements have been met.
Ref: Chemical Fast Sheet for Perfluidone.
Number 74. Date Issued: September 30, 1985.
http://www.fluoridealert.org/pesticides/Perfluidone.Fact.Sheet.1985.htm
-- Potential
of major transformation product (CL 153815) to leach and contaminate
groundwater (page 71) :
--
The major transformation product:
CL 153815 is classified as persistent in soil under anaerobic
conditions (page 22). The transformation product, CL
153815, meets the criterion for persistence in sediment. The
CL 153815 half-life in sediment (645 days) exceeds the TSMP
Track 1 cut-off criterion (≥ 365 days). - (page 44)
Fate
Process for CL 153815 - Major Transformation Product:
(page 71) |
Anaerobic
soil |
persistent |
Aerobic
water layer |
slightly
persistent |
Aerobic
water / anaerobic sediment |
moderately
persistent. |
Anaerobic
water / anaerobic sediment |
persistent |
Anaerobic
water layer |
persistent |
Anaerobic
sediment layer |
persistent |
Ref:
Nov 2005 - AC 900001 (Picolinafen). Proposed Regulatory Decision
Document. PRDD2005-5. Canadian
Pest Management Regulatory Agency (PMRA).
http://www.fluorideaction.org/pesticides/picolinafen.canada.nov05.pdf
Primisulfuron-methyl - Fungicide, Herbicide- CAS No. 86209-51-0
Plant toxicity values
include a duckweed 14-day EC 50 of 0.27
ppb and an algae 7-day EC
50
of 24 ppb. EPA believes that there is sufficient evidence
for listing primisulfuron 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.
Prodiamine
- Herbicide - CAS No. 29091-21-2
Prodiamine: Highly
toxic to fish and invertebrates.
Prodiamine: Eco-Acute Toxicity
-- Rainbow Trout 96-hour LC50 0.83 ppm
-- Bluegill Sunfish 96-hour LC 50 0.55 ppm
-- Daphnia magna 48-hour LC50 0.66 ppm
Ref: 2002 - Material Safety Data Sheet.
Barricade 4FL Herbicide. Syngenta.
http://www.fluoridealert.org/pesticides/Prodiamine.MSDS.Syngenta.02.pdf
Ref:
Acute Aquatic Ecotoxicity Summaries for Prodiamine on Fish,
Pesticide Action Network. http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=29091-21-2&Rec_Id=PC34255&Taxa_Group=Fish |
Common
Name |
Scientific
Name |
Avg Species
LC50 (ug/L) |
LC50 Std
Dev |
Number
of Studies |
Avg Species
Rating |
Fish |
Sheepshead
minnow |
Cyprinodon
variegatus |
450.0 |
- |
1 |
Highly
Toxic |
Channel
catfish |
Ictalurus
punctatus |
76,000 |
24,000 |
2 |
Slightly
Toxic |
Bluegill |
Lepomis
macrochirus |
7,777 |
8,428 |
3 |
Moderately
Toxic |
Rainbow
trout,donaldson trout |
Oncorhynchus
mykiss |
829.0 |
- |
1 |
Highly
Toxic |
Profluralin
- Herbicide
- CAS No. 26399-36-0
--Toxic
to Honey Bees
-- Very High Bioconcentration in Aquatic
Organisms
Ref: TOXNET profile from Hazardous Substances
Data Bank.
http://www.fluoridealert.org/pesticides/Profluralin.TOXNET.HSDB.htm
Prosulfuron
- Herbicide - CAS No. 94125-34-5
Particular conditions
to be taken into account on short term basis by Member States
in relation to the granting of authorisations of plant protection
products containing prosulfuron On the basis of the proposed and
supported uses [herbicide on maize, sorghum
and sweet corn], the following particular issues have been
identified as requiring particular and short term (within 12 months
at the latest) attention from the Member States, in the framework
of any authorisations to be granted, varied or withdrawn, as appropriate:
- Aquatic organisms: Member states must
carefully consider the risk to aquatic plants if the active substance
is applied adjacent to surface waters. The exposure input
from drain flow with respect to local conditions should also be
considered. Risk mitigation measures (e.g. buffer zones) should
be applied where appropriate.
- Leaching to groundwater: Particular attention
should be given to the potential for groundwater contamination,
when the active substance is applied in regions with vulnerable
soil and/or climate conditions. Risk mitigation measures
should be applied where appropriate.
Ref: July 2, 2002 - Review report for the
active substance prosulfuron. European Commission Health &
Consumer Protection Directorate-General.
http://www.fluoridealert.org/pesticides/Prosulfuron.EU.July.2002.pdf
Pyraflufen-ethyl
- Herbicide - CAS No. 129630-19-9
Particular conditions
to be taken into account on short term basis by Member States
in relation to the granting of authorisations of plant protection
products containing pyraflufen-ethyl On the basis of the proposed
and supported uses [herbicide use in cereals], the following particular
issues have been identified as requiring particular and short
term (within 12 months at the latest) attention from the Member
States, in the framework of any authorisations to be granted,
varied or withdrawn, as appropriate:
- Member States must pay particular attention to the protection
of algae and aquatic plants and should apply, where appropriate,
risk mitigation measures.
- The acid metabolite (designated as E1)
has a potential for leaching which might require particular attention
in vulnerable areas to ensure protection of groundwater.
Ref:
July 2, 2002 - Review report for the active substance pyraflufen-ethyl.
Finalised in the Standing Committee on Plant Health at its meeting
on 29 June 2001 in view of the inclusion of Pyraflufen-ethyl in
Annex I of Directive 91/414/EEC. SANCO/3039/99-FINAL. European
Commission Health & Consumer Protection Directorate-General.
http://www.fluoridealert.org/pesticides/Pyraflufen-eth.EU.July.2002.pdf
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