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

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

Picolinafen  - Herbicide - CAS No. 137641-05-5

-- 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
                            

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

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