Quinclorac - Denial of Application to Register 8/01
August 3, 2001
RETURN RECEIPT REQUESTED
Laura L. Whatley, Ph.D.
Senior Registration Scientist
P.O. Box 13528
Research Triangle Park, NC 27709-3528
Dear Dr. Whatley:
Re: Denial of Application to Register the Pesticide Product Drive® 75
DF Herbicide (EPA Reg. No. 7969-130) Containing the New Active Ingredient
The New York State Department of Environmental Conservation
(The Department) has completed review of your application, received on August
22, 2000, and supplemental information submitted to date regarding registration
of the referenced pesticide product in New York State. Drive® 75 DF Herbicide
(EPA Reg. No. 7969-130) contains the new active ingredient quinclorac
Drive® 75 DF Herbicide, containing 75.0% quinclorac, is
labeled for postemergence application to residential and nonresidential
turfgrasses for the control of certain broadleaf and grass weeds. Listed
under the "General Restrictions and Limitations" section of the labeling
is the statement "Do no apply more than 2 pounds of Drive® 75 DF Herbicide
per acre (or 0.73 ounces per 1,000 square feet) in one year." This is
equivalent to a maximum of 1.5 pounds quinclorac per acre per year. Also
listed under the "General Restrictions and Limitations" section of the
labeling is the statement "Do not apply on Long Island in the State of New
York." The application package contained no documentation indicating that
this statement was submitted to, or approved by, the United States Environmental
Protection Agency (USEPA).
The application and data package were deemed incomplete on
October 20, 2000. Although the information submitted by BASF Corp.
(rec'd 01/09/01 subsequent to a request for a 30-day time extension
from the original due date of 12/10/00) did not completely fulfill
the Department's data requirements, the data package was deemed
complete for purposes of technical review on March 8, 2001.
Pursuant to the review time frame specified in Environmental
Conservation Law (ECL) §33-0704.2, a registration decision date
of August 5, 2001 was established.
The Department conducted toxicological, ecological effects
and environmental fate risk assessments for quinclorac and the Drive®
TOXICOLOGICAL RISK ASSESSMENT: Neither
quinclorac nor the Drive® formulated product was very toxic in acute oral,
dermal or inhalation exposure studies in laboratory animals, nor were very
irritating to the eyes or skin (tested on rabbits). Whereas the formulated
product was not a skin sensitizer, the active ingredient had skin sensitizing
properties (tested on guinea pigs).
Quinclorac caused some toxicity in chronic feeding studies.
In a chronic feeding/oncogenicity study in mice, quinclorac caused a
decreased body weight gain at 150 milligrams per kilogram body weight per
day (mg/kg/day); the no-observed-effect level (NOEL) was 38 mg/kg/day.
In rats chronically fed quinclorac, female animals showed a decrease in
body weight gain at 757 mg/kg/day, whereas males showed evidence of an increase
in benign pancreatic tumors at a dose of 487 mg/kg/day. The respective NOELs
were 478 and 385 mg/kg/day. In dogs, decreases in red blood cells and hemoglobin,
reduced body weight gain and food consumption, and increased liver and kidney
weights were reported at 469 and 513 mg/kg/day in females and males,
respectively; the respective NOELs were 140 and 142 mg/kg/day. The USEPA,
Office of Pesticide Programs established a reference dose (RfD) of 0.4 mg/kg/day
based on a NOEL of 38 mg/kg/day in the chronic feeding/oncogenicity study in
mice and an uncertainty factor of 100. This RfD has not yet been adopted by
the USEPA's Integrated Risk Information System (IRIS).
Quinclorac caused some developmental toxicity in the offspring
of pregnant rabbits, but not pregnant rats, fed this chemical during organogenesis
at doses that also caused maternal toxicity. In rabbits, increased resorptions
and post-implantation loss, decrease in number of live fetuses and reduced fetal
body weight were reported at a maternal dose of 600 mg/kg/day; the NOEL was
200 mg/kg/day. Maternal toxicity (decreased body weight gain and food
consumption) occurred at 200 mg/kg/day; the NOEL was 70 mg/kg/day. In
rats, maternal toxicity consisting of increased mortality, decreased food
consumption and increased water consumption occurred at a dose of 438
mg/kg/day; the NOEL was 146 mg/kg/day. No developmental toxicity was observed
at doses of 438 mg/kg/day (the highest dose tested). In a two-generation
reproduction study in rats, a decrease in pup body weights and viability
and developmental delays (eye opening) were reported at a dose of 600 mg/kg/day;
the NOEL was 200 mg/kg/day. Parental toxicity consisting of reduced body weight
gain during the pre-mating periods for both sexes and reduced maternal body weight
during lactation occurred at a dose of 600 mg/kg/day; the parental NOEL was 200
Quinclorac did not cause oncogenic effects in mice, but was
associated with "an equivocal increase of acinar cell adenomas of the pancreas"
(a benign tumor) in male rats. This chemical was negative in a number of
genotoxicity studies. The USEPA classified quinclorac as "Group D -- not
classifiable as to human carcinogenicity."
An occupational and residential/non-residential risk assessment
for dermal and inhalation exposures to quinclorac used on turf was submitted.
For determining margins of exposure (MOEs), the registrant compared estimated
short-term exposures to a NOEL
of 200 mg/kg/day from the oral developmental toxicity study in rabbits
(for the inhalation route of exposure) and a NOEL of 1,000 mg/kg/day
from the 21-day dermal study in rabbits (for the dermal route of exposure).
For intermediate-term exposures, a NOEL of 75 mg/kg/day from the 90-day oral
mouse study (for ingestion exposures) and the NOEL of 1,000 mg/kg/day from the
rabbit dermal study (for dermal exposures) was used. For commercial handlers,
the MOEs were estimated to be about 1000-fold and greater for combined exposures.
These estimates assumed that workers wore gloves, a single layer of clothing and
no respirator as per label requirements. Generally, the USEPA considers MOEs of
100-fold or greater to provide adequate worker protection. For post-application
activities, including lawn mowing and recreational activities on turf, including
children playing, the MOEs were estimated to be about 1,300 and above.
A review of the environmental fate data for quinclorac indicates
that this chemical has the ability to leach through certain soil types and
contaminate groundwater; the adsorption coefficients (Koc) in sand and clay
were reported to be 13 and 54, respectively. These values suggest that
quinclorac has a very high mobility through some soils. In addition, the
application rate for Drive® is not low (340.2 grams quinclorac per acre, a
maximum of twice a year). Accordingly, the label for the Drive® product
states under "Environmental Hazards" that "This chemical has properties
and characteristics associated with chemicals detected in groundwater. The
use of this chemical where soils are permeable, particularly where the water
table is shallow, may result in groundwater contamination."
There are no chemical-specific federal or State drinking
water/groundwater standards for quinclorac. Based on its chemical structure,
this compound falls under the 50 microgram per liter (μg/L) New York State
drinking water standard for "unspecified organic contaminants" (10 NYCRR Part 5,
Public Water Systems).
The available information indicates that the expected direct
exposure from the labeled use of Drive® 75 DF Herbicide should not pose a
significant risk to workers or to the general public. However, there are
concerns for the leaching potential of quinclorac and its ability to
contaminate groundwater/drinking water in vulnerable areas of the State.
ECOLOGICAL EFFECTS RISK ASSESSMENT: Drive® 75 DF
Herbicide is labeled for the control of many broadleaf and grass weeds on
residential and nonresidential turf. It is applied postemergence to actively
growing weeds at 1.0 pound per acre, 0.367 ounce per 1000 square feet, as a
broadcast spray or spot treatment. No more than 2.0 pounds per acre, 1.5
pounds active ingredient, may be applied per year. Drive® may not be applied
aerially or through irrigation systems. Quinclorac is generally considered to
achieve its herbicidal activity through mimicry of the plant hormone auxin.
Technical quinclorac has a water solubility of 64.0 mg/L. Its
vapor pressure is low at 0.75x10-7 mmHg, volatilization will not contribute
significantly to its dissipation. With an octanol/water partition coefficient,
KOW, of 0.266 at pH 7.0, quinclorac should not bioaccumulate. Its 36 ml/g mean
soil organic carbon partitioning coefficient, KOC, indicates that quinclorac may
be very mobile in soil.
Quinclorac is stable to hydrolysis at pH 5.0, 7.0, and 9.0.
It is stable to aqueous photolysis in sterile water, but does undergo photolysis
in the presence of sensitizers such as humic acids, tryptophan, tyrosine,
riboflavin et al., that occur in natural waters. Very little photodegradation
occurred during the submitted 30-day guideline study conducted with sterile
laboratory water. Non-guideline studies and literature reviews submitted to
the USEPA Environmental Fate and Groundwater Branch, however, yielded half-lives,
T1/2, of 24-65 hours in H2O2 solutions, 5-10 days in non-sterilized rice paddy
and river waters, and 22-38 days in buffered solutions containing soil humic
acid and/or rose bengal. Quinclorac has a mean soil surface photolysis T1/2
of 141 days.
Aerobic soil metabolism T1/2 values were reported as 168 days
for a clay soil, 391 days for loamy sand, and "> 1 year" for two silt loam
soils. Extrapolated aerobic half-lives for the two silt loam soils are 1140
to 9125 days. Aerobic aquatic metabolism T1/2s in clay soil/water and loam
soil/water systems were calculated to be 393 and 1229 days, respectively.
Quinclorac is stable to anaerobic aquatic metabolism, T1/2 values from two
studies utilizing two soils each ranged from 1250 to 2520 days.
Data Evaluation Records (DERs) for six terrestrial field
dissipation studies were submitted with the quinclorac data package.
Five of the six turf studies conducted in 1988-89 in California, Georgia,
Missouri, New Jersey, and Oregon, were classified as unacceptable in 1990
when the DERs were produced. The value of the these studies was limited due
to identified deficiencies; no route of dissipation provided, contamination
of control plots, interception by turf not accounted for and variable recovery
of fortified samples. The reported 0-6 inch soil layer dissipation T1/2 values
ranged from 18-166 days. Dissipation half-lives given for these studies only
represent the loss of parent material from the top six inches of the soil profile.
This loss does not represent degradation of the active ingredient but primarily
translocation most likely via leaching and/or runoff. The laboratory degradation
studies, in this case, probably more accurately predict environmental residence
The sixth field dissipation study, an acceptable wheat and
sorghum study, was conducted in Kansas in 1997. In this study spring and
winter quinclorac applications dissipated from upper soil layers with a T1/2s
of 10 and 40 days, respectively. Parent quinclorac was identified in the 42-48
inch deep soil layer 180 days post application at 0.017ppm, representing roughly
1.4% of the applied material. At 21 days post application one metabolite was
found at the 6-12 inch depth at 0.02 ppm (1.6% of applied), at 180 days another
metabolite was identified at the 12-18 inch depth at 0.019 ppm (roughly 1.4% of
Screening level exposure modeling was conducted for
terrestrial and aquatic non-target organisms using highly conservative values
and assumptions. All toxicity and fate parameters were taken from the data
package submitted by the applicant. Terrestrial feeding exposures were modeled
using Hoerger and Kenaga "immediate post application, upper limit vegetation
residue levels." Aquatic runoff modeling assumptions included: no product
interception by target vegetation, 100% of the runoff water reached the model
pond, and no active ingredient degradation between applications.
Model results indicate that no direct toxic effects to fish or
wildlife resources are anticipated through labeled use of Drive® 75 DF Herbicide.
The only toxicity threshold exceeded was the mouse chronic NOEC at the highest
vegetation residue level. Given the highly conservative screening nature of the
modeling conducted for this assessment, actual field vegetation residue levels
are not likely to exceed the mammalian chronic toxicity threshold as predicted
ENVIRONMENTAL FATE RISK ASSESSMENT: Drive® 75 DF
Herbicide (75% quinclorac) is labeled for postemergence control of broadleaf
and grass weeds in residential and nonresidential turf grasses. This product
is foliarly applied and cannot be applied aerially or through chemigation
equipment. The Drive® 75 DF product labeling limits application to 1.5 lb
quinclorac/acre/year. The inerts do not appear to be solvent carriers.
USEPA reviews of quinclorac were generated for products
labeled for aquatic and terrestrial food crop use patterns with a maximum
application rate of up to 0.75 lb quinclorac/acre/year, half of the proposed
Drive® 75 DF Herbicide turf rate. The DERs were produced over a period of
several years as studies were repeated. Information for the Department's risk
assessment was primarily taken from a September 17, 1992 Environmental Fate &
Ground Water Branch (EFGWB) memorandum associated with a rice crop use pattern
and an Environmental Fate and Effects Division (EFED) risk assessment (04/27/99)
accompanying the registration of Paramount Herbicide (EPA Reg. No. 7969-113),
which is labeled for sorghum and wheat.
Hydrolysis: Quinclorac is stable at pHs 5, 7, and 9.
Aqueous Photolysis: Quinclorac is stable to photolysis in sterile
water. A non-acceptable study indicated that quinclorac degraded photolytically
in the presence of non-sterile water with half-lives of 5.3 and 15.7 days.
Soil Photolysis: Relatively stable half-lives of 122-162 days were
found. The EFGWB memo indicates that photodegradation is probably not a major
route of degradation under terrestrial field conditions.
Aerobic Soil Metabolism: Quinclorac is very stable. The half-life
in loamy sand was 391 days, while the half-life in clay soil was 168 days. One
major degradate, 2-OH-514 H, was detected at 14.9%.
Aerobic Aquatic Metabolism: Quinclorac is very stable under aerobic
aquatic conditions with a half-life of >1 year in flooded silty clay and silty
clay loam soils during the 30-day study.
Anaerobic Aquatic Metabolism: Quinclorac is very stable. In
the EFGWB memo, a half- life of >365 days was cited.
Leaching and Adsorption/Desorption: Quinclorac was very mobile
in five soils ranging in texture from sand to silty clay. In general, absorption
increased with increasing soil organic matter content, CEC, and clay content.
Koc values ranged from 13 for the sandy loam to 54 for the clay loam soil.
Leaching and Adsorption/Desorption of the Primary Degradate BH-514-1:
The degradate was mobile to very mobile in five soils ranging in texture from
sand to silty clay. In general, adsorption increased with increasing soil
organic matter content, CEC, and clay content. Koc values ranged from 860
for the sandy loam to 2080 for the silty clay soil.
Field Dissipation: Dissipation half-lives were reported to be
18, 36, 44, 50 and 166 days in five different field studies at an application
rate of 2.0 lb quinclorac per acre. None of the these studies were found to
be acceptable since the authors did not speculate on the route of quinclorac
degradation. In general, quinclorac was not detected below the 12 inch soil
depth. The EFGWB notes that, given the low Kd values reported for quinclorac,
it is feasible that leaching below 12 inches occurred.
USEPA's Comments (04/27/99): Note that the following EFED
comments pertain to an annual quinclorac application rate one-half of the
maximum labeled rate for Drive®.
"Quinclorac laboratory fate data suggest that the compound
is stable to hydrolysis, soil photolysis, and microbially mediated metabolism.
Information regarding the lengthy intervals required between quinclorac use
and the planting of sensitive crops further suggests environmental stability.
The compound is of relatively high aqueous solubility and has a low affinity
for soil organic carbon, factors suggesting that quinclorac is mobile in the
environment. Movement of quinclorac residues by surface runoff may be a
significant mode of dissipation under terrestrial use conditions, especially
if excess precipitation occurs immediately following a quinclorac application."
"EFED has identified two quinclorac metabolites present in both
the aerobic soil metabolism studies and terrestrial field dissipation studies
(BH514-2-OH and BH514-Me ester). Data are needed to confirm the mobility of
these metabolites in soil. Therefore EFED requests that guideline (163-1)
leaching adsorption/desorption studies be performed on these two metabolites."
"Finally, the environmental persistence of quinclorac, its potential
to enter groundwater as modeled by SCI-GROW and indicated in terrestrial field
studies, and the potential for groundwater impacts to non-target crops via
contaminated groundwater all suggest the need for a small-scale prospective
groundwater contamination study for the compound under the expected conditions
of use in wheat and sorghum."
The Drive® 75 DF Herbicide product labeling bears the following
text under the "Environmental Hazards" heading:
"This chemical has properties and characteristics associated with chemicals
detected in groundwater. The use of this chemical where soils are permeable,
particularly where the water table is shallow, may result in groundwater
The Department's groundwater model (LEACHM) was run on
Riverhead soil using a parent Koc of 13 for sandy loam and a degradate
Koc of 860, a half-life of 391 days and an application rate of 1.5 lb
quinclorac/acre/year (maximum use rate) with 14.9% degrading to the
degradate, the model projects breakthrough in the first year, and cyclical
peaks of about 200 parts per billion (ppb) for the parent with one peak at
400 ppb. For the degradate, the model predicts an accumulation of about
100 ppb during the 10-year modeling period.
Running LEACHM on Howard soil using a parent Koc of 54 for
clay loam soil and a degradate Koc of 2080, a half-life of 168 days and an
application rate of 1.5 lb quinclorac/acre/year, the model projects breakthrough
in the second year, and slowly accumulating peaks of about 100 ppb for the parent
with one peak at about 150 ppb. For the degradate, the model predicts an
accumulation of up to 0.3 ppb during the 10-year modeling period.
CONCLUSION: Laboratory fate data indicate that
quinclorac is stable to hydrolysis, photolysis in sterile water, as well as
aerobic and anaerobic metabolism. Terrestrial field dissipation data
indicate that leaching is a route of dissipation, especially if excess
precipitation occurs immediately following application. The product
labeling bears a groundwater contamination advisory. SCI-GROW and LEACHM
modeling predict impacts to groundwater/drinking water. The USEPA had enough
concerns, based on half of the application rate on the proposed label, to
require guideline leaching/desorption studies on two metabolites and to request
a small-scale prospective groundwater contamination study.
When used as labeled, Drive® 75 DF Herbicide has the potential
to adversely impact ground and surface water resources in New York State.
Therefore, the Department hereby denies the application to register Drive® 75
DF Herbicide (EPA Reg. No. 7969-130) in New York State.
BASF Corporation may reapply to register the subject product.
Such an application must be accompanied by a new application fee and meet the
requirements listed in Appendix 1.A. of "New York State Pesticide Product
Registration Procedures" (August 1996). Prior to submitting an application
for any product containing quinclorac, the environmental fate characteristics
should be completely defined (metabolities) and a small-scale prospective
groundwater contamination study should be completed.
Please contact me at (518) 402-8788, if you have any questions
Maureen P. Serafini
Bureau of Pesticides Management
cc: N. Kim/D. Luttinger, NYS Dept. of Health
R. Zimmerman/R. Mungari, NYS Dept. of Ag. & Markets
G. Good/W. Smith, Cornell PMEP