1

UNITED STATES ENVIRONMENTAL PROTECTION AGENCY

WASHINGTON, D.C. 20460

OFFICE OF

PREVENTION, PESTICIDES AND

TOXIC SUBSTANCES

PC Code 129098

DP Barcode D360713, D365942 & D365948

MEMORANDUM

DATE: February 24, 2010

SUBJECT: Tier I Estimated Drinking Waters Concentrations (EDWCs) of Fluazinam

and its Transformation Products for the Use in the Human Health Risk 

Assessment for the Registration of the Following New Food Uses: 

Lettuce, Apples, Carrots and Bulb Vegetables (Crop Subgroup 3-07A)

FROM: José L. Meléndez, Chemist

Environmental Risk Branch V

Environmental Fate and Effects Division (7507P) 

THROUGH: Mah T. Shamim, Branch Chief

Environmental Risk Branch V

Environmental Fate and Effects Division (7507P)

TO: Laura Nollen, Risk Manager Reviewer

Barbara Madden, Review Manager #05

Daniel Rosenblatt, Branch Chief

Risk Integration, Minor Use and Emergency Response Branch

Registration Division (7505P)

AND: Douglas Dotson, Ph.D., Chemist

Christina Swartz, Branch Chief

Registration Action Branch II

Health Effects Division (7509P)

This memo presents the Tier I Estimated Surface Drinking Water Concentrations and 

Estimated Ground Water Concentrations (EDWCs) for Fluazinam and Fluazinam Total 

Residues (parent plus its major transformation products), calculated using the Tier I 

aquatic models FIRST and SCI-GROW, respectively, for use in the human health risk 

assessment. The registrant is seeking registration of the use of fluazinam on lettuce, 

apples, carrots and bulb vegetables (Crop Subgroup 3-07A).
2

The Estimated Drinking Water Concentrations (EDWCs) for Fluazinam and Fluazinam 

Total Residues were calculated based on a maximum application rate of 4.50 lb a.i./A/

season of fluazinam on apples. For the parent fluazinam, the surface water acute value is 

110 ppb, and the chronic value is 0.744 ppb. The groundwater screening concentration is 

0.216 ppb of fluazinam. For the total fluazinam residues (including the parent 

compound), the surface water acute value is 117 ppb and the chronic value is 19.8 ppb. 

The groundwater screening concentration is 0.216 ppb. These values represent upperbound estimates of the concentrations of the chemicals that might be found in surface 

water and groundwater due to the use of fluazinam on apples. EDWCs were calculated 

for total fluazinam residues because the environmental fate studies indicated that the 

parent compound forms transformation compounds which have similar structure to the 

parent under most conditions (as per MARC request, DP Barcode D272624, W. Cutchin, 

4/23/2001).

Should the results of this assessment indicate a need for further refinement, please, 

contact EFED as soon as possible so that the Division may schedule a Tier 2 assessment.

Data Gaps:

The environmental fate database is substantially complete. The following have been 

identified as data gaps: 835.6100: Terrestrial Field Dissipation. The registrant submitted 

two terrestrial field dissipation studies (MRID#s 45584207 and 45584208). These 

studies are currently in review.

And: 835.6100, 835.6200: Environmental Chemistry Methods (ECMs) and Independent 

Laboratory Validations (ILVs) for Soil, Water and Sediment. ECMs, along with 

successful confirmatory method trials (validation) by an independent laboratory (i.e.

ILVs), are required. These ECMs should have limits of quantitation for the residues of 

concern that are lower than the relevant toxicological levels of concern. The latter risk 

assessments indicated concerns for organisms living in freshwater & estuarine/ marine 

bodies of water, and for estuarine/ marine organisms living in the benthos. Therefore, 

ECMs for water and sediment are required in addition to the ECM for soil. The registrant 

is encouraged to submit state-of-the-art ECMs; further, multi-residue methods (MRMs) 

for soil, water and sediment are preferred.

EXECUTIVE SUMMARY 

Fluazinam’s CAS Name is 3-chloro-N-[3-chloro-2,6-dinitro-4-(trifluoromethyl)phenyl]-

5-(trifluoromethyl)-2-pyridinamine, its IUPAC Name is 3-chloro-N-(3-chloro-5-

trifluoromethyl-2-pyridyl)-α,α,α-trifluoro-2,6-dinitro-p-toluidine, its CAS Number is

79622-59-61, and its PC Code is 129098. Fluazinam is a protectant and contact 

fungicide. It is an uncoupler of oxidative phosphorilation in the respiration chain 

involving protonation/ deprotonation (it inhibits fungal respiration, and the production of 

energy within the fungus). Fluazinam is a phenyl pyridinamine (dinitroaniline). The 

structure consists of one phenyl ring with two nitro groups, and a pyridine ring. Both 

rings have a trifluoromethyl group and are monochlorinated. The rings are attached by 

an amine group.
3

Fig. 1. Structure of Fluazinam

The product containing fluazinam is Omega 500F Agricultural Fungicide (EPA Reg. No. 

71512-1). It contains 40.0% fluazinam. It is currently used on potatoes, peanuts, ediblepodded legume vegetables (except peas), bushberry (crop subgroup 13B), brassica (cole) 

leafy vegetables, ginseng, and dry, and succulent bean crop Subgroup 6B (except peas). 

It is being proposed in a Section 3 (IR-4) petition, for use on lettuce, apples, carrots and 

bulb vegetables (Crop Subgroup 3-07A). The application methods vary with the crops. 

For example, aerial applications are allowed only on potatoes, but the material may be 

applied by sprinkler irrigation, or, for brassica leafy vegetables, it may be applied by soil 

incorporation prior to transplanting. 

This is a Tier I screening-level assessment using Tier 1 aquatic models SCI-GROW and 

FIRST for groundwater and surface water, respectively. It was found that the worse case 

scenario was apples, with the highest seasonal application rate, and the highest PCA. In

addition to the EDWC’s for fluazinam, EDWC’s were calculated for total fluazinam 

residues because the environmental fate studies indicated that the parent compound forms 

transformation compounds which are similar in structure to the parent under most 

conditions (for structures, refer to Table A-1 of the Appendix). EFED observed that 

fluazinam does not undergo degradation. Instead, it undergoes transformation into a 

series of products, all of which resemble the parent by way of their chemical structure. 

For the modeling, the EFED assumed that the physicochemical characteristics were 

similar for both the parent and its products (i.e. the total toxic residue approach).

As indicated above, it was assumed that for the total residues of fluazinam, the properties 

of fluazinam were applicable, and were similar for all the metabolites. For example, the 

solubility of fluazinam was assumed to apply to the total residues as well. It was found 

that the solubility of fluazinam depends on the pH. The solubility of the pH 11 solution 

was used in this assessment since it is the highest available value. Using this value 

resulted in an acute concentration that is higher than the solubility of fluazinam at pH 7. 

(Most environmental conditions are close to neutral pH.) This fact constitutes the source 

of highest uncertainty to the assessment, it appears that the input value could have a large

impact on the acute concentration. It was also assumed that the mobility of fluazinam 

was the same to the total residues; this is supported by mobility data for two of the 

metabolites of fluazinam.
4

This assessment was based on the maximum application rate for the crop (apples, 0.45 lb 

a.i./A), the maximum seasonal rate (4.5 lb a.i./A/season), the minimum interval between 

applications (7 days), and the highest PCA (87%). This is the most conservative 

assumption. The total residues approach is also conservative, with uncertainties due to 

unavailability of detailed degradate information. At this time, the persistence of 

fluazinam transformation products is uncertain because the information about these 

compounds from terrestrial field dissipation studies has been deemed invalid. The 

aquatic metabolism studies signal high persistence of such degradates and in the soil 

metabolism studies, generally the degradates were present in relatively small amounts. 

To address this issue, two new terrestrial field dissipation studies have been submitted 

and are currently in review.

No readily available monitoring data are available for fluazinam. It is likely that primary

treatment may reduce the levels of fluazinam due to its high level of binding and its 

tendency to hydrolyze at higher pHs, but the level of reduction is unknown.

Table 1 provides a summary of the Tier 1 modeled drinking water concentrations. 

Should there be a need for additional refinements a more definitive assessment, using the 

Tier 2 aquatic models may be performed at the expenditure of additional resources.

Table 1. Maximum Tier 1 Estimated Drinking Water Concentrations (EDWCs) for 

drinking water assessment based on ground application of fluazinam.

DRINKING WATER SOURCE 

(MODEL USED) 

USE (rate modeled) MAXIMUM ESTIMATED DRINKING WATER 

CONCENTRATION (EDWC) ( ppb)

Groundwater

(SCI-GROW) Fluazinam 

and Total Residues of 

Fluazinam (Including the 

Parent Compound)

Apples (4.50 lb a.i./A/season) Acute and Chronic 0.216

Surface Water

(FIRST) Fluazinam Apples (4.50 lb a.i./A/season) Acute 1101

Chronic 0.744

Surface Water

(FIRST) Total Residues of 

Fluazinam (Including the 

Parent Compound)

Apples (4.50 lb a.i./A/season) Acute 1171

Chronic 19.8

1. This value exceeds the solubility of fluazinam at pH 7 (71 ppb), but is lower than the solubility at pH 11.

PROBLEM FORMULATION

This is a Tier I drinking water assessment that uses modeling and monitoring data, if 

available, to estimate the ground water and surface water concentrations of pesticides and 

transformation products in drinking water source water (pre-treatment) resulting from

pesticide use on sites that are highly vulnerable. This initial tier screens out chemicals 

with low potential risk and provides estimated exposure concentrations for the human 

health dietary risk assessment.

 
5

The last Tier 1 drinking water assessment was issued on 2/7/07, using the FIRST and 

SCI-GROW models, with bushberries being the worst case scenario. The current most 

conservative scenario was now found to be apples (seasonal application rate 4.50 lb 

a.i./A, divided into ten applications, and broadcast spray application method). The 

present action triggers the need for a new drinking waters assessment because the uses 

have a higher seasonal rate of application.

For fluazinam, the following drinking water hypothesis is being employed for this 

assessment:

Fluazinam use in accordance with the label, results in potential contamination of 

both, surface and ground water resources, with fluazinam and its relevant 

transformation products.

The conceptual site model is a generic graphic depiction of the risk hypothesis. Through 

a preliminary iterative process of examining available data, the conceptual model (i.e., 

the drinking water hypothesis) has been refined to reflect the likely exposure pathways 

that are most relevant and applicable to this assessment (refer to Fig. 2).

Fig. 2. Conceptual Model for Drinking Water Assessment for Fluazinam

Fluazinam is applied to the field via ground methods (for apples and other crops) and 

ground and aerial methods (for potatoes only). Crop absorption may be important

because fluazinam has a relatively high tendency to bind, but crop uptake is not expected 

to be important (for its relatively high Kd and KOC values). In addition, spray drift is an 

important factor in the contamination of nearby surface waters because fluazinam is 

applied via ground or aerial spray. As the field may be kept irrigated and the soils are 

wet, large runoff events, accompanied with erosion, may be a factor in horizontal 
6

movement due to the tendency of the chemical to remain bound to the soils (high 

tendency to partition with the soils). Fluazinam shows low persistence in laboratory

studies in aquatic media, but its persistence is higher in soils. It may be available for 

moderate periods of time (on the order of several weeks to several months) in soils; 

fluazinam total residues are persistent in aquatic environments. Vertical movement to 

subsurfaces is not expected to be very important in the dissipation of fluazinam despite its 

moderate persistence in aerobic environments due to its level of binding. Volatilization is 

expected to be a relatively minor route of dissipation for the active ingredient (fluazinam 

has a relatively small vapor pressure and Henry’s Law Constant). The degradates 

observed in the laboratory studies included CAPA, G-504, HYPA AMPA, MAPA, 

DAPA and DCPA, but not all of them are expected to be present in the aquatic 

environment. The major transformation products observed in the aquatic metabolism

studies include DCPA, HYPA, CAPA, DAPA and AMPA. For structures of the various 

transformation products of fluazinam, refer to Table A-1 of the Appendix.

ANALYSIS

Use Characterization

A summary table of all use patterns, new uses and modeled uses, is provided in Table 2. 

The crop groups shaded gray are the proposed ones; the bolded & underlined use is the 

modeled one (apples). This information is based on the current and proposed label of 

Omega 500F, EPA Reg. No. 71512-1.

Table 2. Use information for fluazinam (based on Omega 500F label, EPA Reg. No. 71512-1).

USE

SINGLE APP. 

RATE (lb. 

a.i./A)

NUMBER 

OF APPS.

SEASONAL 

APP. RATE 

(lb. a.i./A)

INTERVAL 

BETWEEN 

APPS. (days) APP. METHOD PHI (days)

Lettuce (head and leaf) 1.00 1 1.00 N/A Ground:

foliar band,

broadcast 

spray or soil 

drench

For head

lettuce 50; 

for leaf 

lettuce 30

Crop Subgroup 3-07A 

Bulb Vegetables (includes 

bulb daylily, bulb fritillaria, 

bulb garlic, bulb great headed 

garlic, bulb serpent garlic, bulb 

lily, bulb onion, bulb Chinese 

onion, pearl onion, bulb potato 

onion, bulb shallot, and 

cultivars, varieties, and/or 

hybrids of these)

0.52 6 3.13 7 - 10 Ground, 

through 

sprinkler 

irrigation

7

Carrots 0.52 4 2.09 7 Ground 7

Apples 0.45 10 4.50 7 - 10 Broadcast 

spray

28
7

Table 2. Use information for fluazinam (based on Omega 500F label, EPA Reg. No. 71512-1).

USE

SINGLE APP. 

RATE (lb. 

a.i./A)

NUMBER 

OF APPS.

SEASONAL 

APP. RATE 

(lb. a.i./A)

INTERVAL 

BETWEEN 

APPS. (days) APP. METHOD PHI (days)

Peanut 0.52-1.04 2 2.09 21 Ground, 

Sprinkler 

irrigation

Do not 

apply w/in 

30 d of 

threshing 

for harvest

Potato 0.18-0.26 7 1.82 7 Aerial, 

Ground, 

Sprinkler 

irrigation

14

Succulent Bean Crop 

Subgroup 6B (such as, but 

not limited to lima bean and 

broad bean)

0.26-0.44 2 0.91 7 Ground, 

Sprinkler 

irrigation

14

Ginseng 0.52-0.78 4 3.13 7 Ground 30

Crop Subgroup 6A, 

Edible-Podded Legume 

Vegetables except peas, 

such as, but not limited to: 

Phaseolus spp. Such as: runner 

bean, snap bean, wax bean; 

Vigna spp. Such as: asparagus 

bean, Chinese longbean, moth 

bean, yardlong bean; jackbean, 

and sword bean

0.26-0.44 2 0.91 7 Ground, 

Sprinkler 

irrigation

14

Dry Bean Crop Subgroup 

6C, except Peas and 

Soybeans (such as, but not 

limited to dried cultivars of 

bean: Lupinus spp.; Phaseolus 

spp, such as kidney beans, dry 

lima bean, navy bean, pinto 

bean; Vigna spp., such as adzuki 

bean; and broad bean, such as 

lablab bean)

0.26-0.44 2 0.91 7 Ground, 

Sprinkler 

irrigation

30

Crop Subgroup 13-07B, 

Bushberry, such as, but not 

limited to: Aronia berry, 

blueberry (highbush and 

lowbush), Chilean guava, 

currant (Buffalo, black, red, and 

Native), elderberry, European 

barberry, gooseberry, highbush 

cranberry, honeysuckle, 

huckleberry, jostaberry, 

juneberry, lingonberry, salal, 

and sea buckthorn

0.65 6 3.90 7 Ground 30
8

Table 2. Use information for fluazinam (based on Omega 500F label, EPA Reg. No. 71512-1).

USE

SINGLE APP. 

RATE (lb. 

a.i./A)

NUMBER 

OF APPS.

SEASONAL 

APP. RATE 

(lb. a.i./A)

INTERVAL 

BETWEEN 

APPS. (days) APP. METHOD PHI (days)

Crop Group 5, Brassica 

(Cole) Leafy Vegetables, 

such as, but not limited to: 

broccoli; broccoli raab (rapini); 

Chinese cabbage (napa); 

cauliflower; collards, kale; 

mizuna; mustard spinach; turnip 

greens; Chinese broccoli; 

Brussels sprouts; Chinese 

cabbage (bok choy); Chinese 

mustard cabbage; cavalo 

broccoli; kohlrabi; mustard 

greens; rape greens

[Transplant 

6.45 fl oz/100 

gal or 

presumably 

0.64 lb a.i./A]

Soil incorporation 1.36 at 

a soil depth 

of 6-8 in

1 2.00 N/A Soil drench 

after 

transplanting

or soil 

incorporation

(transplant 

the seedlings 

into the 

treated band

20;

50 for 

heading 

vegetables 

such as 

cabbage 

and 

broccoli

Fluazinam may be applied through sprinkler irrigation (through center pivot, motorized 

lateral move, traveling gun, solid set or portable1irrigation systems); however, it can also 

be soil incorporated before transplant, for Crop Group 5, brassica (cole) leafy vegetables, 

in soils with low infiltration rates. The label requires a buffer zone of 25 ft within 

permanent bodies of water (lakes, reservoirs, rivers, permanent streams, marshes or 

natural ponds, and estuaries) so as to allow growth of a vegetative filter strip. The 

product should not be applied by aerial equipment within 150 ft of estuarine/ marine 

areas (aerial applications are currently allowed only for potatoes). The product does not 

require a similar buffer zone for aerial applications on freshwater bodies of water (for 

freshwater bodies of water, the 25-ft buffer zone applies).

The four newly proposed uses are lettuce, bulb vegetables (Crop Subgroup 3-07A), 

carrots and apples. Ground application methods are proposed for all those crops. The 

use pattern selected for modeling was apples. It is noted that the highest seasonal 

application rate is 4.50 lb a.i./A applies to apples; meanwhile, the individual single 

application rate is not the highest of all crops. The intervals between applications are 7 

days. It is applied by broadcast spray, which may cause drift towards the index reservoir, 

it also has the highest PCA (default, 87%). With ten applications, at seven-day interval, 

it is likely that this scenario will provide the highest acute and chronic exposure.

Fate and Transport Characterization

A detailed summary of physicochemical and environmental fate/transport properties of 

fluazinam, including measured parameters, values, data sources, and comments, is 

provided in Table 3.

 

1 Wheel move, side roll, end tow, or hand move portable irrigation systems.
9

Table 3. Summary of Various Physicochemical and Environmental Fate Properties of Fluazinam

Parameter Value Reference/Comments *

Selected Physicochemical Parameters

Water Solubility (25oC) 0.025 ppm at pH 5.5; 0.071 ppm at 

pH 7.0; and 350 ppm at pH 11.0

MRID 42208403

Vapor pressure 8.25x10-6 mm Hg MRID 42248403

Molecular Formula C13H4Cl2F6N4O4

Molecular Weight 465.1 g/mol

CAS No. 79622-59-6

CAS name 3-chloro-N-[3-chloro-2,6-dinitro-4-(trifluoromethyl)phenyl]-5-(trifluoromethyl)-2-

pyridinamine

IUPAC name 3-chloro-N-(3-chloro-5-trifluoromethyl-2-pyridyl)-α,α,α-trifluoro-2,6-dinitro-ptoluidine

Henry’s Law Constant 6.73 x 10-7atm-m

3

/mol at pH 7 PMRA Reg. Note REG2003-12

Octanol/Water Partition & log KOW 3620 & 3.56 (at 20°C) MRID 42248403

Persistence: 

 Fluazinam Fluaz.+Degradates 

Hydrolysis t1/2 pH 5

pH 7

pH 9

stable

42 days

6 days

stable

stable

stable

MRID 42208412 (a)

Photolysis t1/2 in water 2.5 days, dark 

control ≈stable

one degradate (G504)MRID 44807312, 43521009, 45584204

(a)

on soil 35.0 days, value 

corrected for dark 

control

degradates at 

≤10% of the 

applied

MRID 44807313, 45584204 (a)

Soil metabolism Aerobic t1/2 114-132 days for 

samples treated at 

1 kg/ha (5.56 ppm)

degradates at 

≤10% of the app.; 

HYPA was 11.4% 

at 30 days (for soil 

treated at 5 kg/ha)

MRID 42208413, 42208414 (a)

Soil metabolism Anaerobic t1/2 SL flooded at time 

0 days – half-life 4 

days;

SL flooded at 30 

days – half-life 32 

days

HYPA was 11.0% 

at 60 days for the 

spl. flooded at 30 

days. MAPA was 

up to 29.8% for the 

sample flooded at 

time 0.

MRID 42208413, 42208414 (s)

Aquatic metabolism Aerobic DT50 4.0-7.4 hours 51-71 days MRID 44807314 (a)

Aquatic metabolism Anaerobic t1/2 ≈ 1⁄3 day (or 

approximately 8

hours)

stable MRID 43521010 (a)
10

Table 3. Summary of Various Physicochemical and Environmental Fate Properties of Fluazinam

Parameter Value Reference/Comments *

Mobility/Adsorption-Desorption

Batch Equilibrium - Unaged

Aged Soil Column Leaching

4 soils KF=11-44 KFOC=1700-2300

 KF, des=34-507 KFOC, des=7000-19900

- - - - - -

0.66% in leachate

MRID 42248628, 42974913 (a)

MRID 42208415 (a)

Batch Equilibrium HYPA

Batch Equilibrium CAPA

6 soils Kd=6.6-51 KOC=640-3200

 KF=4.3-26 KFOC=450-1700

Increasing adsorption w. increasing pH

- - - - - - -

4 soils KF=4.9-67 KFOC=1289-3784

Studies on HYPA and CAPA were 

conducted w. sterile soils.

MRID 43528201 (a)

MRID 44807315 (s)

Field Dissipation

Terrestrial Dissipation

t1/2 in soil surface layer

Range from 9 to 49 days: Ephrata, 

WA: DT50~9 days loamy sand, pinto 

beans; Kempton, ND: half-life=49 

days, sandy loam, beans; Porterville, 

CA: half-life=20 days, loamy sand, 

beans; Montezuma, GA The 

degradation was biphasic.

MRID 44807318, 44807320, 44807316 

(s)

Bioaccumulation

Accumulation in Fish, max. BCF 273-348 X for fillet portion

960-1220 X for whole fish

1410-1850 X for non-edible

~67% of the residues eliminated from the 

fillet during the 21-day depuration phase

MRID 43521012 (a)

(a) = acceptable or core study that fulfills guideline requirement; (s) = supplemental study; (u) = unacceptable study. Where 

two values are stated, they may correspond to two radiolabel positions.

Fluazinam appears to degrade at moderate rates in aerobic soils (132 days), but it is more 

rapidly transformed into other compounds of similar backbone structure in high pH 

solutions (6 days at pH 9) or in aerobic (≤7.4 hr) or anaerobic aquatic (~8 hr) media. The 

transformation products of fluazinam appear to be relatively persistent under most 

conditions. Fluazinam may photolyse relatively rapidly in water (2.5 days) to form a 

tricyclic compound (G-504). The total fluazinam residues (fluazinam and its 

transformation products) are persistent in most environments (stable to hydrolysis at all 

pHs, aerobic aquatic metabolism 51-71 days, relatively stable in anaerobic aquatic

environment) and are likely to reach aquatic media as a totality through runoff. Since 

fluazinam does not alter substantially its backbone structure in the environment, but 

instead, goes through slight transformations of functional groups, EFED considers parent 

and transformation products together when making assessments. Based on the properties 

of the chemical, applications of fluazinam are likely to reach the target (the crop), but 

drift is also possible. The total residues of fluazinam may reach adjacent bodies of water 

via runoff events and may be persistent. The chemical has a low vapor pressure 

(8.25x10-6 mm Hg), and a relatively low Henry’s Law constant (6.73 x 10-7atm-m

3

/mol). 
11

Due to the fact that it appears to show short half lives in aquatic media, and it binds to 

soils, EFED believes that the chemical would not volatilize substantially. While the 

parent and two transformation products, HYPA and CAPA, have relatively low mobility, 

indicating low potential for ground water contamination, there is uncertainty about the 

other transformation products and further information on them was required in a new 

terrestrial field dissipation study. Two such studies (MRID#’s 45584207 & 45584208) 

are currently in review.

Hydrolysis 

The hydrolysis of fluazinam is pH dependent. It was relatively stable at pH 5, and 

hydrolyzed with half-lives of 42 and 6 days at pHs of 7 and 9, respectively. The major 

degradate was CAPA.

Photolysis 

Fluazinam photolyses in aqueous solutions, mainly to G-504, a tricyclic compound, and 

possibly one or more other unidentified products). The half-life obtained in the study

was 2.5 days. The soil photolysis, on the other hand, the half-life was 22 days (compared 

to 69 days for the dark control). The dark control corrected half-life is 35 days.

Metabolism 

The metabolism of fluazinam appears to be moderate in a sandy loam soil treated at 1 

kg/ha (5.56 ppm) (DT50 ≤ 30 days). The calculated half-life (linear regression, assuming 

first order kinetics) was about 114-132 days, which is in agreement with the fact that after 

361 days, 6.8 and 9.5% of the applied fluazinam remained intact for the 14C-pyridyl and 

14C-phenyl labels, respectively. No major metabolites were observed. The sandy loam 

treated at 5 kg/ha yielded a half-life of 227 days. For the samples treated at the high rate,

Compound XII (HYPA) was observed at up to 11.4% at 30 days posttreatment. A loamy

sand treated at 1 kg/ha yielded a half-life of 165 days with no major metabolites. No 

major degradation products were observed in the samples treated at 1 kg/ha, but a major 

fraction (~41%) was bound material at the end of the study (day 361).

Sediment/Water Systems 

The aerobic aquatic and the anaerobic aquatic metabolism studies resulted in very short 

half-lives (4 – 8 hours). In such studies, various metabolites were formed. All the major 

transformation products observed have structures that resemble the structure of the 

parent. The sum of the concentration of the parent, plus the concentrations of the 

transformation products (total fluazinam residues), decreased very slowly under both 

aerobic (half-lives 51-71 days) and anaerobic (relatively stable) aquatic conditions. The 

major transformation products observed in these studies include DAPA, SDS-67200, 

AMPA, DCPA, and CAPA.

Mobility 

In batch equilibrium studies, fluazinam is slightly mobile in four soils tested. KFOC

values ranged from 1705-2316. Similarly, an available soil column leaching study of 

aged fluazinam indicated low mobility of the residues of fluazinam. Less than 1% of the 

applied radiocarbon was found in the leachates and >>80% remained at the top of the soil 
12

columns. There is mobility information for two of the transformation products of 

fluazinam: HYPA and CAPA. Of them, HYPA appeared to be moderately to slightly

mobile (KFOC=450-1700, 6 soils), and CAPA appeared to be slightly mobile, but 

generally less mobile than the parent (KFOC=1289-3784, 4 soils). The latter two 

batch/equilibrium studies were conducted on sterile soils.

Field Dissipation

Four terrestrial field dissipation studies were submitted by the registrant. Such studies 

were found to provide only limited supplemental information. In particular, the data 

about the degradates is very questionable due to poor recoveries in a storage stability

study. In general, it appeared that parent fluazinam degraded moderately rapidly in 

studies conducted in Ephrata, WA, Kempton, ND, Porterville, CA, and Monctezuma, 

GA. The dissipation half-lives ranged from 9 to 49 days. These half-lives are in 

agreement with the aerobic soil metabolism half-lives. At this time, the EFED has two 

newly submitted terrestrial field dissipation studies, which are in review.

Bioaccumulation 

Fluazinam demonstrated some potential to bioaccumulate in fish. The maximum BCF’s 

were 348X for fillet, 1220 for whole fish, and 1850 for viscera, all of which were 

obtained with the phenyl labeled material. Fish residues identified included the parent 

compound, AMPA, MAPA and DAPA. Depuration was moderately slow. More than 

67% of the residues were eliminated from the fillet during the 21-day depuration phase.

The fate and transport characterization also includes the various degradation and 

transformation products formed by each process in the studies reviewed. This is of 

particular importance for fluazinam, which forms metabolites of similar structure than the 

parent compound. Table 4 provides a summary of these transformation products.

Table 4. Summary of degradate formation from degradation of fluazinam.

STUDY TYPE

DEGRADATE and MAXIMUM CONCENTRATION

CAPA, G-504, HYPA AMPA, MAPA, DAPA, DCPA (% applied) SOURCE

Hydrolysis CAPA 34% at 28 days

pH 7; 84-85% at 20 

days at pH 9

– – MRID: 42208412.

Aqueous Photolysis G-504 was 14.0-

17.1% by 7-10 days

_ – MRID: 444807312, 

43521009, 45584204.

Soil Photolysis HYPA, detected > 

dark control

AMPA detected > 

dark control

– MRID: 44807313, 

45584204.

Aerobic Soil Metabolism HYPA, MAPA and DAPA detected (in the SL soils, applied at 1 kg/ha) MRID: 42208413, 

42208414.

Anaerobic Soil Metabolism HYPA was 11.0% at 

60 days for the SL 

flooded at 30 days

MAPA was 29.8% at 

14 days for the SL 

flooded at zero time

– MRID: 42208413, 

42208414.

Aerobic Aquatic Metabolism CAPA 12.6% at 72 hr DAPA: 19.0% by 240 

hr DCPA: 11.3% at 24 hr MRID: 44807314.
13

Table 4. Summary of degradate formation from degradation of fluazinam.

STUDY TYPE

DEGRADATE and MAXIMUM CONCENTRATION

CAPA, G-504, HYPA AMPA, MAPA, DAPA, DCPA (% applied) SOURCE

Anaerobic Aquatic Metabolism AMPA 24.2% at 0.2 

day

DAPA: 32.7% at day 

30

SDS-67200 39.6% by 

day 14

MRID: 43521010.

Terrestrial Field Dissipation MAPA, CAPA, and HYPA were monitored; however, there were 

problems with the storage stability data for the degradates.

MRID: 44807318,

44807320, 44807316, 

44807319, 44807317.

Drinking Water Exposure Modeling

Models

A brief description of the models used follows.

SCI-GROW (v 2.3, 8/5/03) (Screening Concentration in Ground Water) is a regression 

model used as a screening tool to estimate pesticide concentrations found in ground water 

used as drinking water. SCI-GROW was developed by fitting a linear model to 

groundwater concentrations with the Relative Index of Leaching Potential (RILP) as the 

independent variable. Groundwater concentrations were taken from 90-day average high 

concentrations from Prospective Ground Water studies; the RILP is a function of aerobic 

soil metabolism and the soil-water partition coefficient. The output of SCI-GROW 

represents the concentrations that might be expected in shallow unconfined aquifers 

under sandy soils, which is representative of the ground water most vulnerable to 

pesticide contamination likely to serve as a drinking water source. (Ref. 1 & 2)

FIRST (v 1.1.1, 3/26/08) (FQPA Index Reservoir Screening Tool) is a metamodel of 

PRZM and EXAMS used as a screening tool to estimate pesticide concentrations found 

in surface water used as drinking water. FIRST was developed by making multiple runs 

of PRZM using varying sorption coefficients and determining the concentration in the 

EXAMS index reservoir scenario after a two-inch single storm event. (The Index 

Reservoir is a standard water body used by the Office of Pesticide Programs to assess 

drinking water exposure (Office of Pesticide Programs, 2002). It is based on a real 

reservoir (albeit not currently in active use as a drinking water supply), Shipman City

Lake in Illinois, that is known to be vulnerable to pesticide contamination.) The single 

runoff event moves a maximum of 8% of the applied pesticide into the reservoir. This 

amount can be reduced by degradation or effects of binding to soil in the field. 

Additionally, FIRST can account for spray drift and adjusts for the area within a 

watershed that is planted with the modeled crop (Percent Cropped Area). Spray drift 

(modeled as direct deposition of the pesticide into the reservoir) is assumed to be 16% of 

the applied active ingredient for aerial application, 6.3% for orchard air blast application, 

and 6.4% for other ground spray application. Despite being a single event model, FIRST 

can account for spray drift from multiple applications. The default agricultural Percent 

Cropped Area (PCA) is 87%. The PRZM scenario used for FIRST development was 

among the most vulnerable, and thus resulting surface water concentrations represent the 
14

upper bound values on the concentrations that might be found in drinking water from the 

use of a pesticide. (Ref. 1, 3 & 4)

For volatile and semi-volatile compounds, Tier I modeling will tend to over-estimate 

surface water EDWCs because there are no parameters in FIRST that explicitly take into 

account volatility (ie., no vapor pressure or Henry’s Law constant inputs). Therefore, in 

reality, more of the compound will be volatilizing than Tier I can account for. If drinking 

water levels of concern are exceeded for over-estimated Tier I surface water EDWCs, 

Tier II modeling will be able to refine these EDWCs by including volatility, Henry’s 

Law, diffusion in air, and enthalpy considerations. Since SCI-GROW is a regression 

model developed from actual pesticide data with a range of volatilities, systematic 

conclusions cannot be drawn about over or underestimation of groundwater EDWCs at 

Tier I. 

Modeling Approach and Input Parameters

Tables of modeling parameter input values for SCI-GROW and FIRST (Tables 5 & 6, 

respectively) are based on the current input parameter guidance (Ref. 5).

In addition to the EDWC’s for fluazinam, EDWC’s were estimated for the total 

fluazinam residues, because the environmental fate studies indicated that the parent 

compound forms transformation compounds which are similar in structure to the parent 

under most conditions. The input parameters were selected according to the similarity

observed in the mobility characteristics of fluazinam, HYPA, and CAPA. 

It was observed that the KOC model was better to describe the mobility of fluazinam. For 

SCI-GROW, the median value was used, while, for FIRST, the lowest non-sand value 

was selected. Only one value of aerobic soil metabolism was available (it was used in 

SCI-GROW, and three times the value was used in FIRST. Two values of aerobic 

aquatic metabolism were available. For FIRST, the 90th percentile of the upper 

confidence bound on the mean was calculated. It is noted that the input value for the 

aerobic aquatic metabolism of the parent is only 0.454 days (10.9 hours), while for the 

total residues, it is 91.8 days. A ground application method was selected (with 6.4% 

drift). The maximum available solubility value, at 20-25oC was used in modeling, as per 

current guidelines. This solubility applies to a pH 11. It is noted that the solubility of 

fluazinam is pH dependent. 

 

For the total residues, the half-life was calculated taking into consideration the 

transformation products plus fluazinam. This applied to the aerobic aquatic metabolism 

(as indicated earlier, 91.8 days for total residues vs. 0.454 days for fluazinam), and the 

hydrolysis (relatively stable for total residues vs. 42 days for the parent). For the

hydrolysis study, the transformation product that is formed is CAPA. In the aerobic 

aquatic metabolism study, the transformation products formed are DCPA, CAPA, and 

DAPA, plus various minor transformation products. For other parameters, in the absence 

of a suitable value, it was assumed that the value for fluazinam was similar to that for the 

total residues because they had similar structures (e.g. for the solubility).
15

Table 5. SCI-GROW (v 2.3) input parameter values for fluazinam and total residues 

of fluazinam, use on apples1.

PARAMETER (units) FLUAZINAM TOTAL 

RESIDUES

SOURCES AND COMMENTS

Maximum Application Rate (lb a.i./A) 0.45 Proposed label.

Number of Applications per Year 10 Proposed label. Represents most-conservative 

scenario in which the total maximum rate is 

applied in six applications.

Organic Carbon Partition Coefficient 

(Koc; mL/g)

1904.5 Represents the median value of four values 

ranging from 1705 to 2316 mL/g for the parent 

compound. 

Aerobic Soil Metabolism Half-life 

(days)

132 Represents one value for the aerobic soil 

metabolism of the parent compound.

1 Parameters are selected as per Guidance for Selecting Input Parameters in Modeling the Environmental 

Fate and Transport of Pesticides; Version II, February 28, 2002.

Table 6. FIRST (v 1.1.1) input parameter values for fluazinam and total residues of 

fluazinam, use on apples1.

PARAMETER (units) FLUAZINAM TOTAL 

RESIDUES

SOURCES AND COMMENTS

Application Rate (lb a.i./A) 0.45 0.45 Proposed label.

Number of Applications 10 10 Proposed label.

Interval between Applications (days) 7 7 Proposed label.

Percent Cropped Area (decimal) 0.87 0.87 National default.

Soil Partition Coefficient (Kd; (mL/g) or 

KOC (mL/gOC))

1894 1894 Represents the lowest non-sand KOC value among 

four values ranging from 1705 to 2316 mL/g. The 

KOC model is better for this chemical. 

Aerobic Soil Metabolism Half-life 

(days)

396 396 Determined by multiplying the calculated half-life 

(132 days) by 3 to account for the uncertainty 

associated with using a single value.

Wetted in? No No

Proposed label.

Depth of Incorporation (inches) 0.0 0.0

Proposed label.

Method of Application Ground 

application

Ground 

application

Proposed label.

Solubility in Water at pH 11 (mg/L or 

ppm)

350 350

Maximum available value, at 20-25oC.

Aerobic Aquatic Metabolism Half-life 

(days)

0.454 91.8 Represents the 90th percentile of the upper 

confidence bound on the mean of two half-life 

values (4.0 hr and 7.4 hr: mean 5.7 hr, std. dev. 

2.40 hr, the value is 10.9 hr or 0.454 days). For 

total residues two half-lives (51 and 71 days: mean 

61 days, std. dev. 14.14 days)
16

Table 6. FIRST (v 1.1.1) input parameter values for fluazinam and total residues of 

fluazinam, use on apples1.

PARAMETER (units) FLUAZINAM TOTAL 

RESIDUES

SOURCES AND COMMENTS

Hydrolysis Half-life @ pH 7 (days) 42 Stable The transformation product CAPA reaches a 

maximum at the end of the study at pH 7.

Aquatic Photolysis Half-life @ pH 7 

(days)

2.5 2.5 From aqueous photolysis study

1 Parameters are selected as per Guidance for Selecting Input Parameters in Modeling the Environmental 

Fate and Transport of Pesticides; Version II, February 28, 2002.

The Percent Cropped Area (PCA) used was the National Default of 0.87; it is intended 

for use on crops for which no PCA has been developed. Options for Tier I on a national 

scale are cotton, wheat, corn, soybeans, or default. Regional PCAs are a Tier II tool 

intended for refined assessment. (Ref. 6)

Modeling Results

Table 7 summarizes the modeling results for all model runs.

Table 7. Maximum Tier I Estimated Drinking Water Concentrations (EDWCs) for 

drinking water risk assessment based on ground application of fluazinam.

DRINKING WATER SOURCE 

(MODEL USED) 

USE (rate modeled) MAXIMUM ESTIMATED DRINKING WATER 

CONCENTRATION (EDWC) ( ppb)

Groundwater

(SCI-GROW) Fluazinam 

and/or Total Residues of 

Fluazinam

Apples (4.50 lb a.i./A/season) Acute and Chronic 0.216

Surface Water

(FIRST) Fluazinam

Apples (4.50 lb a.i./A/season) Acute 110

Chronic 0.744

Surface Water

(FIRST) Total Residues of 

Fluazinam

Apples (4.50 lb a.i./A/season) Acute 117

Chronic 19.8

The SCI-GROW concentration (ppb) represents the groundwater concentration that might 

be expected in shallow unconfined aquifers under sandy soils. The output is used for both 

acute and chronic endpoints.

The FIRST concentrations (ppb) represent untreated surface water concentrations. The 

one-in-10-year peak day concentration is used for acute endpoints and the one-in-10-year 

annual average concentration is used for chronic endpoints. 
17

The estimated concentrations provided in this assessment are conservative estimates of 

concentrations in drinking water. If dietary risks require refinement, higher tiered cropspecific and location-specific models and modeling scenarios can be used.

Monitoring Data

No readily available monitoring data are available for fluazinam. In general, monitoring 

data provide different kinds of information than modeling estimates. For example, 

monitoring data consist of actual information from the field, reflecting current use pattern 

and usually underestimating frequency of occurrence. Monitoring data does not always 

include peak values, and inputs for monitoring cannot be adjusted as modeled ones can. 

In addition, monitoring is often conducted for purposes other than characterizing 

exposure from a particular pesticide, and as a consequence is used to complement 

modeling rather than to refine it. In general, a useful interpretation of monitoring values 

requires in-depth assessment of the data, which is beyond the scope of a Tier I 

assessment.

Drinking Water Treatment

It is likely that primary treatment may reduce the levels of fluazinam due to its tendency 

to bind. However, there is no information available at this time to determine the levels of 

reduction. Fluazinam is very short lived in aquatic environments, forming various other 

transformation products, which are more persistent. Softening of drinking water will 

generally result in an increase in pH. Fluazinam is more susceptible to hydrolysis under 

alkaline conditions; therefore, softening may result in increased dissipation from 

hydrolysis. (Ref. 9)

CONCLUSIONS 

This is a Tier I level drinking waters analysis, refinements may be available should they

be needed. In addition to the EDWCs for fluazinam, EDWCs were estimated for total 

fluazinam residues because the environmental fate studies indicated that the parent 

compound forms transformation compounds which are structurally very similar to the 

parent under most conditions (for structures, refer to Table A-1 of the Appendix). EFED 

observed that fluazinam was not undergoing degradation. Instead, it was undergoing 

transformation into a series of products, all of which resembled the parent in their 

chemical structure and were more persistent (this is particularly true for the aquatic 

metabolism studies). For the modeling, the EFED assumed that the physicochemical 

characteristics were similar for both the products and the parent. This is named total 

toxic residue approach, which was taken as opposed to the approach that follows the 

formation/ decline of the residues or the approach that assumes an equivalent application 

rate for each metabolite. The two latter approaches require more data than are currently 

available.

Exposure to fluazinam and its residues are possible due to spray drift or runoff. Both the 

aerobic and anaerobic aquatic metabolism studies show half-lives of ≤8 hours for 

fluazinam, with the formation of various metabolites which are much more persistent in 

such media. In soils, fluazinam is more persistent than in aquatic systems (132 days). 

Therefore, exposure to the parent is more likely in soils. In aquatic environments, it 
18

appears that the major exposure will be to the metabolites.

The acute levels of fluazinam in surface drinking waters was 110 ppb, while the chronic 

level was 0.744 ppb. The groundwater concentration of fluazinam, suitable for acute and 

chronic exposure is 0.216 ppb.

For the total toxic residues, the acute levels of surface drinking waters was 117 ppb, the 

chronic level was 19.8 ppb (of total residues). The groundwater concentration of total 

toxic residues of fluazinam, suitable for acute and chronic exposure is 0.216 ppb.

It was assumed that for the total residues, the properties of fluazinam were applicable, 

and were similar for all the metabolites. For example, the solubility of fluazinam was 

assumed to apply to the total residues as well. It was found that the solubility of 

fluazinam depends on the pH. It is higher when the pH is higher (0.025 ppm at pH 5.5, 

0.071 ppm at pH 7.0, and 350 ppm at pH 11.0). The solubility of the pH 11 solution was 

used in this assessment since it is the highest available value at 20-25oC, as per current 

guidelines. Use of this value resulted in an acute concentration that is higher than the 

solubility of fluazinam at pH 7. It is noted that most environmental conditions are close 

to neutral pH. This fact brings uncertainty to the assessment and, since the acute value 

was greater than the solubility of the compound, it appears that the input value could have 

a high impact on the results (particularly on the acute value).

Another example of the assumption that the properties of fluazinam apply to the total 

residues is the mobility. The mobility may be slightly different for each transformation 

product. It was found that the KOC model was more suitable to describe the mobility of 

fluazinam than the Kd model. The batch equilibrium studies performed on the degradates 

HYPA and CAPA show that the mobility of such metabolites is similar to that of the 

parent (for the parent, KFOC=1700-2300; for HYPA, KFOC=450-1700; and for CAPA, 

KFOC=1289-3784, refer to Table 3). Nonetheless, the studies conducted on HYPA and 

CAPA were conducted on sterile soils.

The aerobic soil metabolism input value for the FIRST model was determined by 

multiplying the available half-life (132 days) by 3 to account for the uncertainty

associated with using a single value. This is considered a conservative assumption for 

the model.

This assessment was based on the maximum application rate for the crop (apples, 0.45 lb 

a.i./A), with the maximum seasonal rate (4.5 lb a.i./A/season), with the minimum interval 

between applications (7 days), and the highest PCA (0.87 or 87%). For apples, the 

maximum application rate of 0.45 lb a.i./A is recommended for certain species (Bitter rot, 

Black rot, Brooks spot, Cedar apple rust, Alternaria blotch, White rot, Quince rust, Twospotted spider mite, European red mite and Apple rust mite). Meanwhile, for Apple 

Scab, Flyspeck and Sooty blotch, the recommended application rate range is 0.33 to 0.45 

lb a.i./A and the interval between applications is 7 to 10 days. The proposed label 

indicates that “the high rate and shortest intervals should be used for more susceptible 

varieties and heavy disease pressure.” The maximum application rate and the crop 
19

scenario (apples) may not be representative for all the crops registered or proposed on a 

national scale basis. It is uncertain whether apples will represent a major use for 

fluazinam. However, this use is the most conservative assumption.

The total residues approach is conservative, with uncertainties due to unavailability of 

detailed degradate information. A more definitive assessment, using the Tier 2 aquatic 

models may be performed at the expenditure of additional resources, and given the 

availability of additional data. The assessment could involve input from additional 

studies (not available at this time, e.g. the detailed formation and decline data for the 

metabolites) and refine the PCAs (e.g., by using regional PCAs). Also, typical 

application rates may be used, when and if available.

No readily available monitoring data are available for fluazinam. It is likely that primary

treatment may reduce the levels of fluazinam due to its tendency to bind and its highest 

susceptibility to hydrolysis under alkaline conditions. However, there is no information 

available at this time to determine the levels of reduction. Furthermore, fluazinam is very

short lived in aquatic environments, but it forms various other transformation products, 

which are more persistent in the media.

*****************************************************************

References:

1. Policy Establishing Current Versions of Exposure Models and Responsibility for 

Model Maintenance (11/06/2002)

2. SCIGROW: Users Manual (11/01/2001, revised 08/23/2002)

3. FIRST Users Manual (08/01/2001)

4. FIRST: A Screening Model to Estimate Pesticide Concentrations in Drinking 

Water (05/01/2001)

5. Guidance for Selecting Input Parameters in Modeling the Environmental Fate and 

Transport of Pesticides, Version II (02/28/2002) 

6. Use of the Index Reservoir and Percent Crop Area in EFED Drinking Water 

Assessments (12/01/1999)

7. Golf Course Adjustment Factors for Simulated Aquatic Exposure Concentrations 

(06/01/2005)

8. Policy for Estimating Aqueous Concentrations from Pesticides Labeled for Use 

on Rice (10/29/2002)

9. The Incorporation of Water Treatment Effects on Pesticide Removal and 

Transformations in Food Quality Protection Act (FQPA) Drinking Water 

Assessments (10/25/2001)

*****************************************************************
20

APPENDIX

Table A-1. Fluazinam and Various Transformation Products

Common 

Name

Chemical Name Structure

Fluazinam CAS Name: 3-chloro-N-[3-chloro2,6-dinitro-4-(trifluoromethyl) 

phenyl]-5- (trifluo-romethyl)-2-

pyridinamine;

IUPAC Name: 3-chloro-N-(3-

chloro-5-trifluoromethyl-2-

pyridyl)-α,α,α-trifluoro-2,6-dinitrop-toluidine

CAPA 3-chloro-6-(3-chloro-2,6-dinitro-4-

trifluoromethyl anilino)nicotinic 

acid;

5-chloro-6-(3-chloro-α,α,αtrifluoro-2,6-dinitro-ptoluidino)nicotinic acid

N

H

N

O2N

O2N

Cl

CF3

Cl

HOOC

DAPA 3-chloro-N

4

-(3-chloro-5-

trifluoromethyl-2-pyridyl)-α,α,αtrifluorotoluene-3,5,5-triamine; 3-

chloro-2(2,6-diamino-3-chloroα,α,α-trifluoro-p-toluidino)-5-

(trifluoromethyl) pyridine

N

H

N

H2N

CF3

Cl

H2N

Cl

F3C

DAPA

AMPA 2-(6-amino-3-chloro-α,α,α-trifluoro2-nitro-p-toluidino)-3-chloro-5-

(trifluoromethyl)pyridine

N

H

N

O2N

H2N

Cl

CF3

Cl

F3C

DCPA 6-(4-carboxy-3-chloro-2,6-

dinitroanilino)-5-chloronicotinic 

acid

N

H

N

O2N

COOH

Cl

O2N

Cl

HOOC

DCPA
21

Table A-1. Fluazinam and Various Transformation Products

Common 

Name

Chemical Name Structure

MAPA 3-chloro-N

4

-(3-chloro-5-

trifluoromethyl-2-pyridyl)-5-nitroα,α,α-trifluoro-toluene-3,4-diamine

N

H

N

H2N

O2N

Cl

CF3

Cl

F3C

HYPA,

Compound XII

5-[[3-chloro-5-(trifluoromethyl-2-

pyridyl]amino]-α,α,α-trifluoro-4,6-

dinitro-o-cresol

N

H

N

O2N

CF3

HO

O2N

Cl

F3C

G-504 4,9-dichloro-6-nitro-8-

(trifluoromethyl)pyrido-[1,2-α]-

benzimidazole-2-carboxylic acid

N

N

O2N

CF3

Cl

Cl

HOOC
22

SCIGROW and FIRST model output files:

 SCIGROW

 VERSION 2.3

 ENVIRONMENTAL FATE AND EFFECTS DIVISION

 OFFICE OF PESTICIDE PROGRAMS

 U.S. ENVIRONMENTAL PROTECTION AGENCY

 SCREENING MODEL

 FOR AQUATIC PESTICIDE EXPOSURE

SciGrow version 2.3

chemical:Fluazinam

time is 11/ 4/2009 12:10:11

------------------------------------------------------------------------

 Application Number of Total Use Koc Soil Aerobic

 rate (lb/acre) applications (lb/acre/yr) (ml/g) metabolism (days)

------------------------------------------------------------------------

 0.450 10.0 4.500 1.90E+03 132.0

------------------------------------------------------------------------

groundwater screening cond (ppb) = 2.16E-01 

************************************************************************

RUN No. 1 FOR Fluazinam ON Apples * INPUT VALUES *

--------------------------------------------------------------------

RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE %CROPPED INCORP

ONE(MULT) INTERVAL Koc (PPM ) (%DRIFT) AREA (IN)

--------------------------------------------------------------------

0.450( 4.261) 10 7 1894.0 350.0 GROUND( 6.4) 87.0 0.0

FIELD AND RESERVOIR HALFLIFE VALUES (DAYS)

--------------------------------------------------------------------

METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

(FIELD) RAIN/RUNOFF (RESERVOIR) (RES.-EFF) (RESER.) (RESER.)

--------------------------------------------------------------------

396.00 2 0.00 2.50- 310.00 0.45 0.45

UNTREATED WATER CONC (MICROGRAMS/LITER (PPB)) Ver 1.1.1 MAR 26, 2008

--------------------------------------------------------------------

PEAK DAY (ACUTE) ANNUAL AVERAGE (CHRONIC)

CONCENTRATION CONCENTRATION

--------------------------------------------------------------------

110.468 0.744
23

RUN No. 2 FOR Total Res ON Apples * INPUT VALUES *

--------------------------------------------------------------------

RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE %CROPPED INCORP

ONE(MULT) INTERVAL Koc (PPM ) (%DRIFT) AREA (IN)

--------------------------------------------------------------------

0.450( 4.261) 10 7 1894.0 350.0 GROUND( 6.4) 87.0 0.0

FIELD AND RESERVOIR HALFLIFE VALUES (DAYS)

--------------------------------------------------------------------

METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

(FIELD) RAIN/RUNOFF (RESERVOIR) (RES.-EFF) (RESER.) (RESER.)

--------------------------------------------------------------------

396.00 2 N/A 2.50- 310.00 91.80 70.83

UNTREATED WATER CONC (MICROGRAMS/LITER (PPB)) Ver 1.1.1 MAR 26, 2008

--------------------------------------------------------------------

PEAK DAY (ACUTE) ANNUAL AVERAGE (CHRONIC)

CONCENTRATION CONCENTRATION

--------------------------------------------------------------------

116.750 19.777