Risk quotients for herbivores/ insectivores mostly exceed the restricted use and listed species acute levels of concern for the turf use sites for all weight classes of mammals in all food categories with the exception of the large insect category. Additionally, listed species levels of concern were exceeded for pecan, stone fruit, and grasses grown for seed for 15 and 35 g mammals for multiple applications to mammals 2 Appraisal of the Safety of Chemicals in foods, Drugs and Cosmetics. Association of Food and Drug Officials of the United States. 3rd Printing, 1975. Page 56 of 206 foraging on short grass and small insects. The RQ for peanut exceeds the listed species LOC for 15 g mammals under the multiple application scenario. None of these RQs are reduced below the LOCs when a 14.41 foliar dissipation half life is used. The results of these RQs are presented below. RQs did not exceed any levels of concern for granivores.

Mammalian Herbivore/ Insectivore Risk Quotients Exceeding LOC Based on Single and Multiple Applications with a mouse LD50 of 729 mg ai/ kg bw Use site Food Type Weight Class of Mammal ( g) Single Appl. Residue RQ Multiple Appl Residue RQ 15  0.07 *** Stone fruits   ( apricot, cherry, nectarine, peach, and plum) and nonbearing crops ( maximum 0.1125 lb ai/ A; 5 appl.; 5 day intervals) Short grass 35  0.06 ***

15  0.09 *** Pecan, Grasses grown for seed ( forage fodder grasses ( maximum 0.225 lb ai/ A; 4 applications; 14 day interval Short grass 35  0.08 ***

Peanut   ( maximum 0.225 lb ai/ A; 2 appl.; 10 day intervals) Short grass 15  0.06***

15 0.25 ** 0.77 * 35 0.22 ** 0.66 * Short grass 1000 0.12 *** 0.35 ** 15 0.14 *** 0.44 ** 35 0.12 *** 0.37 ** turf and ornamentals   ground cover, ( maximum 1.78 lb ai/ A; 4 appl.; 10 day intervals) Small insects 1000 0.07 *** 0.20 ** 15 0.25 ** 0.70 * 35 0.22 ** 0.60 * Short grass 1000 0.12 *** 0.32 ** 15 0.14 *** 0.40 ** 35 0.12 *** 0.24 ** turf and ornamentals   lawns and turf , golf course, ( maximum 1.78 lb ai/ A; 4 appl.; 14 day intervals) Small insects 1000 0.07 *** 0.18 ** 15 0.25 ** 0.61 * 35 0.22 ** 0.52 ** Short grass 1000 0.12 *** 0.28 ** 15 0.14 *** 0.34 ** 35 0.12 *** 0.29 ** turf and ornamentals   sod farm ( maximum 1.78 lb ai/ A; 4 appl.; 21 day intervals) Small insects 1000 0.07 *** 0.16 **

* indicates an exceedance of Acute Risk LOC; RQ > 1.0. ** indicates an exceedance of Acute Restricted Use LOC; RQ > 0.20 *** indicates an exceedance of Listed Species Level of Concern ( LOC); RQ > 0.10.

Calculations for mammalian organisms use both dietary based and oral dosebased risk quotients for calculation of chronic mammalian risk. The NOAEC of 500 mg ai/ kg diet based on reduced body weight gains in F0 and F1 generations in a 2 generation Page 57 of 206 rat study was used for the dietary based RQs. No clinical mortality was observed in the study but hepatic " clear cell change" occurred at the 500 mg ai/ kg diet concentration ( NOAEC = 100 mg ai/ kg diet) in the F0 generation. Since the hepatic cell change was only observed in the F0 generation, chronic RQs were calculated with the NOAEC of 500 mg ai/ kg diet based on reduced body weight gains. The chronic mammalian RQs exceed the chronic LOC for multiple applications to turf use sites and range from 1.1 to 2.3. However, the RQs can be reduced below the chronic LOCs if a 14.41 foliar half life is used for RQ calculations. These RQs are summarized below for the turf uses. Page 58 of 206 Table 4 3. Mammal Reproduction Risk Quotient Calculations based on NOEC of 500 mg/ kg diet Wildlife Food Item Wildlife Food Item Residue Single Application ( mg/ kg diet) Wildlife Food Item Residue Multiple Applications ( mg/ kg diet) Chronic Threshold ( mg/ kg diet) Single Application Reproduction RQ Multiple Application Reproduction RQ turf and ornamentals   ground cover, ( maximum 1.78 lb ai/ A; 4 appl.; 10 day intervals)

short grass 427 1301 500 0.85 2.6   tall grass 196 596 0.39 0.92 broadleaf forage/ small insects 240 732 0.48 1.4   fruit, pods, seeds, large insects 27 81 0.054 0.16 turf and ornamentals   lawns and turf, golf course ( maximum 1.78 lb ai/ A; 4 appl.; 14 day intervals)

short grass 427 1182 500 0.85 2.3 *

tall grass 196 542 0.39 1.1 *   broadleaf forage/ small insects 240 665 0.48 1.33 *   fruit, pods, seeds, large insects 27 74 0.054 0.148 turf and ornamentals sod farm ( maximum 1.78 lb ai/ A; 4 appl.; 21 day intervals)

short grass 427 1008 500 0.85 2.0 *

tall grass 196 466 0.39 2.0 *   broadleaf forage/ small insects 240 572 0.48 1.14 *   fruit, pods, seeds, large insects 27 64 0.054 0.128 RQ = Residue/ Toxicity Threshold Risk Presumption RQ Level of Concern * Chronic Risk 1 * LOC not exceeded if 14.41 day foliar dissipation half life is calculated from T REX.

The dose based RQs can be calculated using the chronic reproductive effect NOAEC of 500 mg/ kg diet. This dietary NOAEC was converted to a NOAEL of 25 mg/ kg bw according to the following formula based on a standard FDA lab rat conversion:

Adjusted NOAEL= NOAEL * ( test species body weight/ assessed body weight) 0.25 The RQs are calculated by obtaining an equivalent dose EEC which is adjusted for the percent body weight consumed for a 15, 35, and 1000 g mammal and dividing this EEC by the adjusted NOAEL. The results for these calculations are summarized for the uses which exceed Page 59 of 206 the chronic LOCs and indicate that RQs exceed the chronic level of concern for all weight classes of mammals foraging on short grass, tall grass, broadleaf plants, small insects, and fruits, pods, and large insects and range from 1.2 to 22.6 for use on turf. Pecans and grasses grown for seed exceed chronic LOCs for 15 and 35 g mammals foraging in short grass, tall grass, and broadleaf plants and small insect categories. LOCs are also exceeded for 1000 g mammals foraging in short grass. Similarly, the RQs exceed the chronic LOC for 15 and 35 g mammals foraging on all the fore mentioned food types plus fruits, pods, and large insects. Finally, LOCs are exceed for 15 and 35 g mammals foraging in short grass and broadleaf plants and small insect food categories for use on peanut and stone fruit. These RQs are summarized below.

Mammalian chronic Oral DOSE based risk quotients for propiconazole when dietary NOAEC of 500 mg/ kg diet is converted to a NOAEL of 25 mg/ kg bw based on a standard FDA lab rat conversion1 Turf ( 1.78 lb ai/ A; 4 applications/ yr at 10 day intervals)

15 g mammal 35 g mammal 1000 g mammal Oral Dose based RQs ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 1240 55 22.6+ 857 44.5 19.3+ 199 19.2 10.3+

Tall Grass 569 55 10.4+ 393 44.5 8.8+ 91 19.2 4.7+

Broadleaf plants/ sm insects 698 55 12.7+ 482 44.5 10.9+ 112 19.2 5.8+

Fruits/ pods/ lg insects 78 55 1.41+ 54 44.5 1.2+^ 12 19.2 0.65 Seeds ( granivores) 17 55 0.31 12 44.5 0.27 2.8 19.2 0.14 Pecans and Grasses grown for seed ( 0.225 lb ai/ A; 4 applications/ yr at 14 day intervals) 15 g mammal 35 g mammal 1000 g mammal Oral Dose based RQs ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 142 55 2.6+ 98 44.5 2.2+ 23 19.2 1.2+

Tall Grass 65 55 1.2+ 45 44.5 1.0+ 10 19.2 0.54 Broadleaf plants/ sm insects 80 55 1.5+ 55 44.5 1.3+^ 13 19.2 0.67 Fruits/ pods/ lg insects 8.9 55 0.16 6.2 44.5 0.14 1.4 19.2 0.07 Seeds ( granivores) 2.0 55 0.04 1.4 44.5 0.03 0.32 19.2 0.02 Peanut ( 0.225 lb ai/ A; 2 applications/ yr at 10 day intervals) 15 g mammal 35 g mammal 1000 g mammal Oral Dose based RQs ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 93.72 55 1.7+ 64.77 44.5 1.46+ 15.02 19.2 0.78 Tall Grass 42.95 55 0.87 29.69 44.5 0.67 6.88 19.2 0.36 Broadleaf plants/ sm insects 52.72 55 0.96+^ 36.45 44.5 0.82 8.45 19.2 0.44 Fruits/ pods/ lg insects 5.86 55 0.11 4.05 44.5 0.09 0.94 19.2 0.05 Seeds ( granivores) 1.30 55 0.02 0.90 44.5 0.02 0.21 19.2 0.01 Stone fruits   ( apricot, cherry, nectarine, peach, and plum) and non bearing crops ( maximum 0.1125 lb ai/ A; 5 appl.; 5 day intervals) Oral Dose based RQs 15 g mammal 35 g mammal 1000 g mammal Page 60 of 206 ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 106.5 55 1.94+ 73.7 44.5 1.66+ 17.1 19.2 0.89 Tall Grass 48.9 55 0.89 33.8 44.5 0.76 7.8 19.2 0.41 Broadleaf plants/ sm insects 60.0 55 1.09+ 41.4 44.5 0.93 9.6 19.2 0.50 Fruits/ pods/ lg insects 6.6 55 0.12 4.6 44.5 0.1 1.1 19.2 0.06 Seeds ( granivores) 1.48 55 0.03 1.0 44.5 0.02 0.24 19.2 0.01 1 The oral dose based RQs are calculated by dividing the EEC equivalent dose by the adjusted NOAEL for chronic values) for each food category and animal class. + exceeds Chronic LOC (> 1.0) * LOC not exceeded if 14.41 day foliar dissipation half life is calculated from T REX.

The dose based chronic RQs may also be calculated when the mammalian chronic study reports the endpoint as mg ai/ kg  bw/ day. This is the preferred method that EFED uses for interpretation of chronic mammalian risk. This study reported the NOAEL as 43 mg ai/ kgbw day. When this NOAEL is adjusted the RQs on turf range from 3.3 to 13 for all weight classes of mammals foraging on short grass, tall grass, broadleaf plants, and small insects. The RQs for pecan, stone fruits, and grasses grown for seed only exceed the LOCs for 15 and 35 g mammals foraging in short grass. Very few of these RQs are reduced below the LOCs when the 14.41 day foliar half life is use for RQ calculations. The results are presented in the table below.

The chronic LOC is not exceeded for any granivores.

Mammalian chronic Oral DOSE based risk based on the reported NOAEL of 43 mg ai/ kg bw1 Turf ( 1.78 lb ai/ A; 4 applications/ yr at 10 day intervals)

15 g mammal 35 g mammal 1000 g mammal Oral Dose based RQs ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 1240 95 13.0+ 857 76 11.3+ 199 33 5.9+

Tall Grass 569 95 5.6+ 393 76 5.18+ 91 33 2.7+

Broadleaf plants/ sm insects 698 95 7.3+ 482 76 6.36+ 112 33 3.3+

Fruits/ pods/ lg insects 78 95 0.81 54 76 0.71 12 33 0.36 Seeds ( granivores) 17 95 0.18 12 76 0.16 2.8 33 0.06 Pecans and Grasses grown for seed ( 0.225 lb ai/ A; 4 applications/ yr at 14 day intervals) 15 g mammal 35 g mammal 1000 g mammal Oral Dose based RQs ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 142 95 1.51+ 98 76 1.29+* 23 33 0.69 Tall Grass 65 95 0.69 45 76 0.59 10 33 0.32 Broadleaf plants/ sm insects 80 95 0.85 55 76 0.72 13 33 0.39 Fruits/ pods/ lg insects 8.9 95 0.09 6.2 76 0.08 1.4 33 0.04 Seeds ( granivores) 2.0 95 0.02 1.4 76 0.02 0.32 33 0.0 Stone fruits   ( apricot, cherry, nectarine, peach, and plum) and non bearing crops ( maximum 0.1125 lb ai/ A; 5 appl.; 5 day intervals) Oral Dose based RQs 15 g mammal 35 g mammal 1000 g mammal Page 61 of 206 ( daily dose/ adjusted NOAEL) EEC residue Adj. NOAEL Chronic RQ EEC residue Adj NOAEL Chronic RQ EEC Residue Adj NOAEL Chronic RQ Short Grass 106.5 95 1.13+* 73.7 76 0.96 17.1 33 0.52 Tall Grass 48.9 95 0.52 33.8 76 0.44 7.8 33 0.24 Broadleaf plants/ sm insects 60.0 95 0.63 41.4 76 0.54 9.6 33 0.29 Fruits/ pods/ lg insects 6.6 95 0.07 4.6 76 0.06 1.1 33 0.03 Seeds ( granivores) 1.48 95 0.02 1.0 76 0.01 0.24 33 0.01 1 The oral dose based RQs are calculated by dividing the EEC equivalent dose by the adjusted NOAEL for chronic values) for each food category and animal class. + exceeds Chronic LOC (> 1.0) * LOC not exceeded if 14.41 day foliar dissipation half life is calculated from T REX.

4. Non target Terrestrial Plants The EC25 value of the most sensitive species in the seedling emergence study is compared to runoff and drift exposure to determine the RQ ( EEC/ toxicity value). The EC25 value of the most sensitive species in the vegetative vigor study is compared to the drift exposure to determine the acute RQ. Non listed and listed species RQs resulting from single applications are calculated for the most sensitive monocot and dicot species for ground and aerial applications. The non listed terrestrial plant RQs indicate that only turf use sites are the major concern for dicot species. The RQs that exceed the LOCs range from 2.1 to 4.6. The listed terrestrial plant RQs for single applications exceed the LOC for for grasses grown for seed, wild rice, and peanut in addition to turf use sites observed for the non listed plant species. The RQs ranged from 1.0 to 8.0 Acute Terrestrial Plant Risk Quotient Calculations For Single Spray Applications of Propiconazole1 Use Site Scenario EC25 ( lb ai/ A) RQ ( Plants Adjacent Treated Site) RQ ( Plants in Semi Aquatic Areas) Drift RQs Method of Application ( Aerial/ ground)

mono > 1.5 Seedling emerg. Dicot 0.18 2.1/ 2.5 Chemigation/ Ground mono 0.315 Turf & Ornamental   ( 1.78 lb ai/ A) Veget. Vigor. Dicot 0.039 2.3/ 4.6 Chemigation/ Ground Acute Listed Terrestrial Plant Risk Quotient Calculations For Single Spray Applications of Propiconazole1 Use Site Scenario NOAEC/ EC05 ( lb ai/ A) RQ ( Plants Adjacent Treated Site) RQ ( Plants in Semi Aquatic Areas) Drift RQs Method of Application ( Aerial/ ground)

mono 1.5 Seedling emerg. Dicot 0.056 1.01 Aerial mono 0.0185 Grasses grown for seed, Wild rice, Peanut ( 0.225 lb ai/ A) Veget. Vigor. Dicot 0.056 Aerial Page 62 of 206 mono 1.5 Seedling emerg. Dicot 0.056 1.0/ 2.3 6.7/ 8.0 Chemigation/ ground mono 0.0185 4.8/ 9.6 Chemigation/ ground Turf & Ornamental   ( 1.78 lb ai/ A) Veget. Vigor. Dicot 0.056 1.6/ 3.2 Chemigation/ ground 1 For purposes of clairty, only the RQs which exceed the LOCs are shown.

Acute risk quotients are derived using the TerrPlant model ( Appendix E) and use the EC25 as the toxicity endpoint. Single applications are calculated using the TerrPlant EECs and are based on the highest single application rate. Runoff exposure estimates are based on the water solubility and the amount of pesticide present on the soil surface and its top one inch. It can be characterized as " sheet runoff" ( one treated acre to an adjacent acre) for dry areas, or as " channelized runoff" ( 10 treated acres to a distant low lying acre) for semi aquatic areas. The percent runoff values are 1, 2, and 5 percent for a water solubility of < 10 ppm, 10 100 ppm, and > 100 ppm, respectively. To account for the amount of pesticide in the top one inch of soil, the application rate is reduced proportionally by the soil depth incorporation in centimeters.

Spray drift exposure from ground and overhead chemigation applications is assumed to be 1% of the application rate. Drift from aerial, airblast, and forced air applications is assumed to be 5% of the application rate. Since EFED does not have data to show residue accumulation from multiple applications over time, the effects of multiple applications are addressed by summing the application rates from individual applications and inputing these values in the TerrPlant model.

There are several uncertainties regarding risk to plants. One is whether the default assumption of 5% spray drift ( from aerial application) in TerrPlant is sufficiently protective. Estimates made from actual drift assessments range to higher than 20%, which could indicate that risk to plants is underestimated. Another uncertainty regarding the model used in this assessment is an assumption that a certain percentage of the applied chemical might be attributed to runoff after an aerial or chemigation application. Formerly EFED used an ` efficiency factor'of a 60% to runoff after aerial application, but the use of this factor appeared to leave about 35% of the applied chemical unaccounted for and it is possible that risk to wetland plants is underestimated. Recently, however, EFED dropped the use of this 60% ` efficiency factor'.

Chronic or reproductive risks to plants are not currently evaluated. Additionally, because of the proposed use on turf and ground cover, RQs for direct application of propiconazole are calculated based on application rate. Federally listed plant species risk quotients are calculated using the NOAEC or EC05.

B. Risk Description A number of papers suggest that conazole type fungicides can potentiate the toxicity of other pesticides. The mechanism by which conazoles increase toxicity is not well understood and likely varies depending on the class of the co occurring pesticide. Conazole fungicides have been documented to induce the production of metabolic enzymes ( cytochrome p450) that convert phosphorothioate insecticides to their more toxic oxon forms. This mechanism has been Page 63 of 206 proposed to explain the synergistic effects to birds of coexposure to phosphorothioates and conazoles ( Walker 1998). In vivo synergism is not always noted with co exposure of phosphorothioates and conazoles with varying effects noted with different animal species, phosphorothioates, and conazole fungicides ( Ronis and Badger 1995, Levine and Oris 1999). Conazole fungicides have been noted to increase the toxicity of neonicotinoid insectides to honey bees ( Iwasa et al 2004). Propiconazole increased the toxicity of three neonicotinoids by a factor ranging from 1 ( no increase in toxicity) to 559 ( increasing the toxicity 559 times) depending on the insecticide tested. P450 enzymes are not required to activate neonicotinoids and an explanation for the synergistic effect of co exposure to conazoles and neonicotinoid insecticides was not provided.

The available literature demonstrates that in some instances co exposure of conazole fungicides and at least two classes of insecticides can result in greater toxicity to fish, birds, and mammals than would be expected from adding the effects of exposure to the chemicals alone. Presently information is not available to determine how often co exposure to potentially synergistic chemicals occurs nor the mechanism of synergism understood well enough to determine when synergism can be expected or the magnitude of potentiation. Thus, this assessment does not quantitatively address the effects of exposure to pesticides in combination with propiconazole exposure.

1. Risks to Aquatic Organisms a. Aquatic Animals Fish and Aquatic Phase Amphibians As described in the Risk Estimation section, the risk quotient of 0.05 is equivalent to the listed species LOC for freshwater fish for use of propiconazole on turf, based on EECs from the Pennsylvania turf scenario using the maximum application rate and minimum application interval for this use. The EECs for the same applications in the Florida turf scenario do not result in RQs that exceed the listed species LOC. Therefore, the potential for risk to listed fish appears to be dependent in part on the soil and weather conditions of the area in which propiconazole is applied to turf.

Since the RQ from the Pennsylvania turf scenario is equivalent to the LOC of 0.05, small changes in the modeling input to PRZM/ EXAMS would reduce the RQ below the LOC. For instance, if less than the maximum rate or number of applications are used, or if a longer application interval is used, then the exposure would result in an RQ that would be below the level of concern. Furthermore, submission of acceptable aerobic aquatic metabolism data could result in a half life shorter than the default value used in the absence of data.

In addition, the labeled turf use includes lawns, sod farms, golf courses, and other types of turf grass. EFED just published ( June 1, 2005) a guidance document   " Golf Course Adjustment Factors for Simulated Aquatic Exposure Concentrations." These golf course adjustment factors ( GCAF) should only be used to refine EECs for turf in a golf course use scenario. Therefore, the exposure values derived from turf scenarios would need to be adjusted Page 64 of 206 specifically to represent the golf course uses. Unless the golf course is treated 100% ( tees, greens, fairways and roughs), the aquatic exposure values from golf course use need to be adjusted by 0.05, 0.29, 0.66, and 0.34, respectively for tees and greens, fairways, roughs, and the combination of tees, greens, and fairways. When the proper GCAF was considered, the listed species LOC would not be exceeded for golf course uses of propiconazole.

Among the aquatic exposures described previously, the rice use represents the most conservative estimates, which assumes the exposure concentrations directly from the rice paddy discharge water. As a result, the listed species LOCs are exceeded for freshwater fish. The propiconazole label specifically forbids rice use in California, so the potential rice exposures will occur in Texas, Arkansas, and Louisiana; both freshwater and estuarine marine fish could potentially be exposed to propiconazole applied to rice in these states.

The finding of risk from use on rice is uncertain because the model does not simulate degradation of the pesticide in rice paddy water before the water is released to drainage canals. Aerobic aquatic metabolism data are not available to estimate how quickly propiconazole might degrade in paddy water, although the aqueous photolysis study suggests that this would be an important route of quick dissipation. A supplemental aqueous dissipation study supports that dissipation may occur quickly in the paddy, with an observed half life of less than 5 days.

Aquatic Invertebrates Risk quotients for the use of propiconazole on turf ( both scenarios) and rice exceed the listed species level of concern for estuarine and marine invertebrates, based on the results of the mysid shrimp study. The RQs for the turf use range are 0.07 and 0.08. Therefore, since the RQs are so near the listed species LOC, additional information that would allow a refinement of input parameters to PRZM/ EXAMS could lead to RQs below the LOC, as described above. The RQs for the rice use are more than 5 times the LOC ( RQ= 0.27), but the potential for quick aquatic dissipation renders this finding of potential risk uncertain, as described in the paragraph above.

Valid chronic data on freshwater invertebrates are lacking at this time and it is therefore not possible to evaluate the chronic effects to aquatic freshwater invertebrates. However, as described above if the available chronic daphnid study could be upgraded to supplemental status, the NOAEC based on mortality and reproduction could be 310 µ g/ L. A chronic study such as this would put RQs based on peak water concentrations below chronic levels of concern.

b. Aquatic Plants Risk quotients for propiconazole only exceeded the acute and listed LOC for nonvascular aquatic plants, based on toxicity to the marine diatom Skeletonema costatum and the freshwater diatom Navicula pelliculosa. It is not possible to determine whether the listed species LOC is also exceeded for vascular plants or for other non vascular plants, because NOAECs could not be established in some toxicity studies. Effects were observed at the lowest concentration tested in studies with vascular aquatic plant Lemna gibba, and in studies with algae species Selenastrum capricornutum and Anabena flos aquae. Therefore, potential indirect effects to listed aquatic animals that depend on aquatic plants other than diatoms cannot be dismissed. Page 65 of 206 2. Risks to Terrestrial Organisms Risk to birds and mammals were evaluated using the risk quotient methold for dietary and dosebased exposure scenarios using the T REX program ( version 1.2.3). As discussed in the Measure of Exposure Section, a 35 day foliar dissipation half life was deemed most appropriate for use with this model. However, data from a " magnitude of the residue" studies can not be completely ignored as studies which were done on wheat had time 0 samples and no indication that rainfall had occurred during the studies. The resulting foliar dissipation half lives from these studies is 14.41 days. Therefore, characterization of terrestrial risk examined the use both half life values. As stated in the Measure of Exposure Section, there is much uncertainty associated with the use of a foliar dissipation half life from the " magnitude of residue" studies.

a. Terrestrial Animals Birds The avian oral and dietary acute toxicity tests indicated that propiconazole is practically non toxic to birds. However, the acute dietary LOC for birds is exceeded for turf uses due to the high use rates and multiple applications. However, there is much uncertainty associated with this risk since a definitive LC50 was not obtained. Dose based RQs based on the oral LD50 marginally exceeded the listed species LOCs for a number of additional uses and reduction in use rates for these sites might help to reduce RQs below these levels of concern. It should also be noted that most all of these RQs could be reduced below all acute LOCs if the 14.41 day foliar half life is considered.

Both dose based and dietary risk was evaluated, however, because a definitive LC50 could not be determined, some uncertainties are associated with the dietary risk quotients. The risk quotients which led to the finding of risk were based on the results of the bobwhite quail acute oral test, since a definitive LD50 could not be established in the mallard duck test. Therefore, there is some uncertainty about how broadly applicable the risk indicated by the screening level assessment is across bird species. Two additional species ( Japanese quail and Peking duck) were included in acute dietary toxicity tests, but these tests do not reduce the uncertainty, since they were only tested at one concentration in the diet ( 1000 mg/ kg diet) that was below the level recommended in the study guideline.

Although the acute toxicity tests could not establish firmly that mortality would occur across a range of bird species from exposure to propiconazole, other effects were observed in the acute studies that could impact the ability of exposed birds to survive in the wild. The acute dietary study for bobwhite quail established an LD50 of 2825 mg/ kg bw. No mortality was observed at the next lowest dose, and only 10% mortality was observed at the dose below that ( reported as 1590 and 1000 mg/ kg bw, respectively). However, lethargy was observed at all doses, including the lowest dose of 398 mg/ kg bw. Reduced reaction to stimuli was observed at the 1000 mg/ kg bw dose, and loss of coordination, wing droop, and lower limb weakness were observed at the two highest doses. Page 66 of 206 Such effects from propiconazole exposure could make affected birds more vulnerable to predation and less able to forage for food, care for young, or reproduce, at least temporarily. Surviving bobwhite quail in the acute oral study recovered fully from these effects by 12 days after dosing. Mallard ducks in the acute oral study suffered lethargy at the highest dose of 2510 mg kg/ bw, but recovered within 6 hours. Mallards and bobwhite quail tested in the acute dietary study did not exhibit these effects, but exhibited reduced feed consumption at higher dose levels.

Chronic Risk Chronic data for birds showed no treatment related effects at any of the test levels up to 1000 mg/ kg diet, and as described in the Effects Characterization, a definitive LOAEL could not be determined. Consequently, the actual NOAEL could be much greater than observed in the study. Hence, there is a great uncertainty when this information is used to evaluate chronic risk to birds. Dietary based chronic RQs to birds were exceeded only for multiple applications to turf and the highest RQ was 1.3. Hence, there is a great uncertainty when this information is used to evaluate chronic risk to birds. A repeat of this study that could produce a NOAEC at a higher concentration could reduce these RQs below all levels of concern. It should be noted that the use of a 95th percentile 14.41 day half life reduces all chronic risk below all chronic LOC.

Mammals Acute risk to mammals based on an adjusted LD50 of 729 mg/ kg bw demonstrated risks to mammals foraging on short grass and small insects; however, the RQs did not exceed the acute risk LOCs. Only restricted use and listed species LOCs were exceeded. Single applications only demonstrated listed species risk to turf for 15 and 35 g mammals, but only for mammals foraging in short grass. However, these risks could be reduced below all LOCs if the calculated foliar half life of 14.41 days was considered.

Chronic risks to mammals were calculated using both the dietary and dose based RQs. Dietary based RQs only exceeded the chronic LOCs for multiple applications to turf and ranged from 1.1 to 2.6 when a default foliar half life of 35 days is used in exposure calculations. However, when a 14.41 foliar half life is used, these LOCs are not exceeded.

Dose based chronic risk demonstrated RQs ranging from as high as 13 to 22 for mammals foraging in short grass. To better understand these effects it is useful to look at the duration of the effects. The tables below show that chronic LOCs are exceeded for up to 52 days after 4 applications for mammals foraging on short grass for the turf scenario. The table also shows that chronic LOCs do not begin to be exceeded until the third application, and these residues drop below the LOCs after 32 days. However, the chronic RQs do not exceed any chronic LOCs after two applications. Page 67 of 206 Page 68 of 206 Terrestrial Residues ( upper bound estimates)

vs Mammalian Herbivore/ Insectivore LOCs ( as dietary concentrations 0.00 200.00 400.00 600.00 800.00 1000.00 1200.00 1400.00 1600.00 1800.00 2000.00 0 4 8 12 16 20 24 28 32 36 40 44 48 52 56 60 64 68 72 76 80 84 88 92 96100 Days Concentration (

mg ai/

kg dietary item) Short Grass Tall Grass Broad Fruits/ pods/ seeds/ lg insects Chronic LOC 15 g M 35 g Mammal Acute LOC 1000 g Mammal Acute LOC 15 g E 35 g Endangered Mammal Acute LOC 1000 g Endangered Mammal Acute LOC Page 69 of 206 b. Terrestrial Plants Although propiconazole is manufactured for its fungistatic mode of action, it potentially poses a risk to terrestrial plants. Risk quotients described in the risk estimation section indicate a risk to non listed ( for turf uses) and listed dicots ( for grasses grown for seed, rice, wild rice, peanut, and turf uses) when considering effects endpoints observed in seedling emergence tests. It is notable that cabbage ( EC25 0.18 lb ai/ acre) was the only dicot affected in the seedling emergence studies. No other plants showed any effects in this study, in which the highest dose tested was 1.5 lb ai/ acre. TERR PLANT ( version 1.2.1) calculates the risk to terrestrial plants in adjacent dryland and semi aquatic areas by comparing the runoff and drift exposure to the most sensitive endpoint from the seedling emergence test. Therefore, while risk to plants from runoff exposure was indicated for all crops on which propiconazole is used, the risk from seedling emergence effects may possibly be limited to a small subset of sensitive dicots. The reader should note that there is a large number of dicot plant families in the United States and the limited number of plant species included in the existing effects database may or may not be fully representative of all these families.

A broader range of monocots and dicots exhibited sensitivity in vegetative vigor tests. Propiconazole was shown to be toxic to 6 of 10 crops tested in the Tier II vegetative vigor study. The NOAEC and EC25 for corn, for instance, were 0.167 and 0.968 lb ai/ acre respectively; the maximum label rate for use of propiconazole on corn allows four annual applications of 0.45 lb ai/ acre. The most sensitive endpoints among the three monocots and three dicots tested were reductions in plant height ( monocots) and reductions in plant height, shoot length and dry weight ( dicots). As a result, RQs calculated for the aerial application to corn from estimated spray drift alone exceed the listed species level of concern for monocots. The use on turf is the only use for which spray drift alone results in an RQ above the non listed LOC ( for dicots only). Drift from the use on turf alone also exceeds the listed species levels of concern for monocots and dicots. Although these listed species RQs were calculated using toxicity data for the most sensitive species, the LOC would still be exceeded if data for the next most sensitive monocot and dicot were used. While this represents only four of the nine species tested, this suggests that a broader range of listed plants could be affected by vegetative vigor effects from exposure to propiconazole.

The TERR PLANT exposure model calculates risk quotients such as those reported in the Risk Estimation section for terrestrial plants for only a single pesticide application. Since propiconazole labels allow multiple applications to each crop, the magnitude of the risk to plants is uncertain, and potentially underestimated. The upper bound to the magnitude of the RQs for terrestrial plants would be to sum the exposures from each application as if the effect to nontarget plants were additive. The resulting RQs, which are shown in the table below for the purpose of risk characterization only, would indicate a potential risk to non endangered plants a wider range of crops than had been calculated for a single application.

However, additional information on the effect of propiconazole on terrestrial plants would be needed to evaluate the uncertainty in multiple application terrestrial plant RQs. The effects of multiple applications could only be additive if the affected plants could not recover from the effects of successive applications. If the plants could recover over time, the effect of Page 70 of 206 multiple applications could be greater for crops that are treated at the shortest application intervals.

The uncertainty in the magnitude of exposure to multiple applications of propiconazole is even greater. The risk quotients for terrestrial plants assume exposure both through spray drift and runoff from a treated field after a heavy rain event. The likelihood of co occurrence of such events is uncertain, especially for multiple applications, and as a result the estimated exposure values may be conservative. In addition, while the likelihood of exposure to non target plants through drift alone is significantly higher, the same plants may not be exposed to spray drift from each application, since wind speed and direction could be different at the time of each application.

Acute Terrestrial Plant Risk Quotient Calculations For Multiple Spray Applications of Propiconazole Use Site Scenario EC25 ( Toxicity Threshold) ( lb ai/ A) RQ ( Plants Adjacent Treated Site) RQ ( Plants in Semi Aquatic Areas Drift RQ Method of Application ( Aerial/ ground)

mono > 1.5 Seedling emerg. Dicot 0.18 3.1 Aerial mono 0.315 Citrus ( nonbearing   ( maximum 0.225 lb ai/ A; 3 apps. at 30 day intervals) Veget. Vigor. Dicot 0.039 1.8 Aerial mono > 1.5 Seedling emerg. Dicot 0.18 1.05/ 1.25 Ground/ Aerial mono 0.315 Aerial Tree nuts ( maximum 0.225 lb ai/ A; 4 applications; 14 day interval) Veget. Vigor. Dicot 0.039 1.15 Ground/ Aerial Acute Listed Terrestrial Plant Risk Quotient Calculations For Multiple Spray Applications of Propiconazole Use Site Scenario NOEC/ EC05 ( Toxicity Threshold) ( lb ai/ A) RQ ( Plants Adjacent Treated Site) RQ ( Plants in Semi Aquatic Areas Drift RQ Method of Application ( Aerial/ ground)

mono 1.5 Seedling emerg. Dicot 0.056 2.1/ 2.5 Ground/ Aerial mono 0.0185 1.5 Aerial Stone Fruit ( 0.1125 lb ai/ A, 5 appl) Veget. Vigor. Dicot 0.056 mono 1.5 Seedling emerg. Dicot 0.056 1.3 Aerial 3.4/ 4.01 Ground/ Aerial mono 0.0185 1.1 Aerial Grasses Grown for seed ( 0.225 lb ai/ A, 4 appl) Veget. Vigor. Dicot 0.056 2.4 Aerial mono 1.5 Seedling emerg. Dicot 0.056 1.7/ 2.0 Ground/ Aerial mono 0.0185 4.9 Aerial Corn, celery ( 0.1125 lb ai/ A, 4 appl) Veget. Vigor. Dicot 0.056 1.2 Aerial Wild rice Seedling mono 1.5 Page 71 of 206 emerg. Dicot 0.056 1.3/ 1.5 Ground/ Aerial mono 0.0185 ( 0.225 lb ai./ A, 3 appl) Veget. Vigor. Dicot 0.056 mono 1.5 1.0/ 1.2 Ground/ Aerial Seedling emerg. Dicot 0.056 3.8/ 8.9 26.7/ 31.8 Ground/ Aerial mono 0.0185 3.9/ 19.2 Ground/ Aerial Turf & Ornamental   ( 1.78 lb ai/ A, 4 appl) Veget. Vigor. Dicot 0.056 1.7/ 6.4 Ground/ Aerial The risk quotients for terrestrial plants assume exposure both through spray drift and runoff from a treated field after a heavy rain event. The likelihood of co occurrence of such events is uncertain, especially for multiple applications, and as a result the estimated exposure values may be conservative. However, the likelihood of exposure to non target plants through drift alone is significantly higher.

The following results of a Tier 1 AgDrift modeling simulation give an indication of the risk to plants that might occur even if runoff from a treated field does not occur at or soon after the time of application. Pesticide application was simulated using low boom ground spray equipment to turf, using nozzles which produce a very fine to fine droplet size spectrum. Using the 90th percentile drift data generated by the Spray Drift Task Force on which AgDrift is based, the model predicted the distances to which point exposure would be equivalent to the EC25 values for various crops tested in the propiconazole vegetative vigor studies.

EC25 ( test crop) Turf ( 1.78 lb ai/ a) Application 0.968 lb ai/ A ( corn) 0.334 lb ai/ A ( onion) 0.16 lb ai/ A ( soybean) 0.039 lb ai/ A ( cabbage) Distance of deposition 3.3 ft 6.6 ft 13.1 ft 42.7 ft The results indicate that exposure that would result in risk quotients at the acute LOC would be expected to occur within 50 feet of turf treated with propiconazole. An additional calculation was done to determine the distance at which point deposition would be equivalent to the lowest NOAEC in the vegetative vigor test ( 0.0185 lb ai/ A for ryegrass). The calculated distance of 91.86 suggests that listed plants more than 100 feet of a treated field may be at less risk.

The next highest application rate for propiconazole after turf is 0.225 lb ai/ acre for grasses grown for seed, pecan, and rice, which is lower than the EC25 for all but soybeans and cabbage in the vegetative vigor test. However, drift from aerial application of 0.225 lb ai/ acre could result in point deposition equal to the cabbage vegetative vigor EC25 of 0.039 lb ai/ A up to a distance of 49 feet, assuming a default fine to medium droplet size spectrum. Drift from aerial application of 0.225 lb ai/ acre could result in point deposition equal to the ryegrass vegetative vigor NOAEC of 0.0185 lb ai/ A up to a distance of 118 feet, assuming the same fine to medium droplet size spectrum. Page 72 of 206 3. Endocrine Disruption Assessment The potential for endocrine disruptor related effects was observed in mammalian and avian toxicity studies submitted to the Agency. In the 2 generation reproduction study with rats ( MRIDs 00163164, 00151514), reduced body weight gains in F0 and F1 generations was observed with a reported NOAEL of 43 mg/ kg bw/ day ( 500 mg ai/ kg diet). Additionally, hepatic " clear cell change" was observed in the F0 generation. Decreased offspring survival and body weights and increased incidence of hepatic lesions ( cellular swelling) at the 2500 mg ai/ kgdiet level were also observed. Chronic data for birds showed no treatment related effects at any of the test levels up to 1000 mg/ kg diet, but a definitive LOAEL could not be determined. Consequently, the actual NOAEL could be much greater than observed in the study. Hence, there is a great uncertainty when this information is used to evaluate chronic risk to birds. However, based on the data available for mammals, the observed reproductive effects could be an indicator of potential endocrine disruption.

There are a number of degradates of tetraconazole, including 1,2,4 triazole, which are formed by biotic and abiotic processes. To date, none of these degradates have been identified as possessing the potential for endocrine disruption. In addition, the registrant has not submitted, nor has the Agency requested, studies on the potential for endocrine disruption for any of these degradates resulting from the use of tetraconazole. Until such time as the Agency determines that any of these degradates have the potential to be an endocrine disruptor, this risk assessment has not included an evaluation of the relative risk of propiconazole degradates for endocrine disruption and as such is a source of uncertainty in this assessment.

EPA is required under the Federal Food, Drug, and Cosmetic Act ( FFDCA), as amended by the Food Quality Protection Act ( FQPA), to develop a screening program to determine whether certain substances ( including all pesticide active and other ingredients) " may have an effect in humans that is similar to an effect produced by a naturally occurring estrogen, or other such endocrine effects as the Administrator may designate." Following the recommendations of its Endocrine Disruptor Screening and Testing Advisory Committee ( EDSTAC), EPA determined that there were scientific bases for including, as part of the program, the androgen and thyroid hormone systems, in addition to the estrogen hormone system. EPA also adopted EDSTAC's recommendation that the Program include evaluations of potential effects in wildlife. For pesticide chemicals, EPA will use The Federal Insecticide, Fungicide, and Rodenticide Act ( FIFRA) and, to the extent that effects in wildlife may help determine whether a substance may have an effect in humans, FFDCA authority to require the wildlife evaluations. As the science develops and resources allow, screening of additional hormone systems may be added to the Endocrine Disruptor Screening Program ( EDSP). When the appropriate screening and/ or testing protocols being considered under the Agency's EDSP have been developed, propiconazole may be subjected to additional screening and/ or testing to better characterize effects related to endocrine disruption.

4. Review of Incident Data Incident information from the Ecological Incident Information System ( EIIS) database was available and indicated that a total of six incidents occurred in conjunction with the use of Page 73 of 206 propiconazole. Four of these 6( a) 2 incident data involved damage to terrestrial plants, and the remaining two reported damage to fish and shrimp. There is a great deal of uncertainty concerning the credibility of these incidents since measured environmental residue data were not reported at any of these sites. All events were rated " possible" as opposed to probable or highly probable. In addition, the incident involving a kill of 1500 fish (# I014538 013) appears to result from an attempt to clean up a spill of several products ( Daconil, Banner, and Dylox) at a golf course in Indiana. Clearly, this incident resulted from a misuse of the product( s) which were rinsed into a creek. The other aquatic incident reported to have taken place at a shrimp farm (# I004697 061) had scant information and could have resulted from contamination from benlate as well as propiconazole. No other details were available from the report including the location of the incident ( county, state, etc.), how or why the spray occurred, or if the shrimp farm was in close proximity to the application site.

Regarding the four incidents to terrestrial plants, detailed information about the damage to the crops/ plants was not provided. It was reported that 12 of the 16 acres of nectarines sprayed by propiconazole ( Break) were " damaged;" however, the description, extent of the damage, or if recovery occurred was not reported (# I007644 16). Another reported incident took place in France, and it appears that 80% leaf damaged occurred on 19 rose trees (# I12786 002). Again, details are not provided regarding the extent of the damage or the impact on the roses. The remaining incidents appear to be related to a misuse of the product even though the details regarding application are somewhat vague. The reported incident of leaf burn to 120 acres of spring wheat in North Dakota (# I015291 045) was due to the application of the product STRATEGO during unfavorable weather conditions ( cool prior to application). The final incident (# I014029 99 006) involving STRATEGO applied to winter wheat in Virginia reported the primary cause as poor mixing of the adjuvant.

5. Federally Threatened and Endangered ( Listed) Species Concerns a. Action Area For listed species assessment purposes, the action area is considered to be the area affected directly or indirectly by the Federal action and not merely the immediate area involved in the action. At the initial Level I screening assessment, broadly described taxonomic groups are considered and thus conservatively assumes that listed species within those broad groups are co located with the pesticide treatment area. This means that terrestrial plants and wildlife are assumed to be located on or adjacent to the treated site, and aquatic organisms are assumed to be located in a surface water body adjacent to the treated site. The assessment also assumes that the listed species are located within an assumed area that has the relatively highest potential exposure to the pesticide, and that exposures are likely to decrease with distance from the treatment area. The Use Characterization section of this risk assessment presents the pesticide use sites that are used to establish initial co location of species with treatment areas.

If the assumptions associated with the screening level action area result in RQs that are below the listed species LOCs, a " no effect" determination conclusion is made with respect to listed species in that taxa, and no further description of an action area is necessary. Furthermore, RQs below the listed species LOCs for a given taxonomic group indicate no concern for indirect Page 74 of 206 effects upon listed species that depend upon the taxonomic group covered by the RQ as a resource.

However, in situations where the screening assumptions lead to RQs in excess of the listed species LOCs for a given taxonomic group, a potential for a " may affect" conclusion exists and may be associated with direct effects on listed species belonging to that taxonomic group or may extend to indirect effects upon listed species that depend upon that taxonomic group as a resource. In such cases, additional information on the biology of listed species, the locations of these species, fate and transport properties of the chemical, and the locations of use sites could be considered to determine the extent to which screening assumptions regarding an action area apply to a particular listed organism. These subsequent refinement steps could consider how this information would impact the action area for a particular listed organism and may potentially include areas of exposure that are downwind and downstream of the pesticide use site.

b. Taxonomic Groups Potentially at Risk The Level I screening assessment process for listed species uses the generic taxonomic group based process to make inferences on direct effect concerns for listed species. The first iteration of reporting the results of the Level I screen is a listing of pesticide use sites and taxonomic groups for which RQ calculations reveal values that meet or exceed the listed species LOCs. In the majority of cases, the screening level risk assessment process reports RQ calculations for the following broad taxonomic groupings:

! Birds ( also used as surrogate for terrestrial phase amphibians and reptiles)

! Mammals ! Freshwater fish ( also used as a surrogate for aquatic phase amphibians)

! Freshwater invertebrates ! Estuarine/ marine fish ! Estuarine/ marine invertebrates ! Terrestrial plants ! Algae and aquatic plants There may also be taxonomic groups of listed species for which screening tools are not fully developed nor represented through surrogacy with existing tools. For example, there is no RQ calculation process for terrestrial invertebrates.

The available screening level information for propiconazole suggests a potential concern for direct effects on listed freshwater fish, estuarine/ marine invertebrates and non vascular aquatic plants only associated with the use on turf. A potential concern for direct effects on birds and mammals is suggested for use on grasses grown for seed, stone fruit, rice, wild rice, and turf and ornamentals. In addition, there is a potential concern for a direct effect on terrestrial plants for uses associated with barley, rye, triticale, stone fruit, grasses grown for seed, corn, celery, wild rice and turf.

1. Discussion of Risk Quotients Page 75 of 206 As summarized in the Risk Characterization section of this assessment, listed species LOCs are exceeded for freshwater fish, estuarine/ marine invertebrates, non vascular aquatic plants, birds, mammals, and terrestrial plants. The LOCATES database was used to identify those U. S. counties where both, all the use sites occur, and have federally listed species. A preliminary analysis has been conducted of this county overlap of crop and listed species.

Freshwater Animals and Aquatic Plants Listed species acute risk RQs exceed the listed species LOCs for freshwater fish, estuarine/ marine aquatic invertebrates, and aquatic plants only for rice and turf and ornament use sites. For the turf and ornamental use sites the freshwater fish RQ of 0.05 is equivalent to the listed species LOC and risk to these species could be eliminated by slightly reducing the use rate for turf. The same reasoning applies to the estuarine/ marine invertebrate RQ of 0.15 which just exceeds the acute LOCs for listed species and restricted use. However, there are currently no listed estuarine/ marine invertebrates and it is safe to say that this group of aquatic animals could be eliminated from listed species concerns. Aquatic plant risk RQs did not exceed acute or listed species LOCs for the turf use sites.

When propiconazole is used on rice the RQ of 0.16 exceeds the acute restricted use LOC for freshwater fish. The estuarine/ marine fish RQ of 0.06 just exceeds the listed species LOC. Modicum reductions in the use rate could reduce these RQs below the listed species LOCs. The estuarine/ marine invertebrate RQ of 0.27 exceeds the acute restricted use and listed species LOC, but as previously mentioned there are currently no listed estuarine/ marine invertebrates.

Birds The RQs only exceed the listed species LOC for 20 g birds foraging in short grass at the corn, celery, stone fruit, rice, and grasses grown for seed sites, and only when maximum residues are considered. The RQs range from 0.05 to 0.08 and are only exceeded if the RQs are rounded to the first decimal. The mean residue LOCs are not exceeded for any of these use sites. These use sites could be eliminated from listed species concerns if the use rates were slightly reduced.

The acute listed species RQs for the turf use sites exceed the acute LOCs for all weight classes of birds when maximum residues are considered. The RQs range from 0.1 to 0.7. If the mean residue values are considered, the LOCs are exceeded only for 20 and 100 g birds and range from 0.1 to 0.25. Chronic risk to birds could not be evaluated due to the uncertainty of the NOAEC and LOAEC values. The dietary based RQs exceed the chronic LOC only for birds foraging in short grass and ranged from 1.0 to 1.3.

Mammals Listed species dose based RQs exceed the acute mammalian LOCs only for multiple applications on grasses grown for seed, stone fruit, rice, and wild rice for 15 and 35 g mammals foraging in short grass. These RQs range from 0.06 to0.09. As stated for birds, a slight reduction in these rates could reduce the RQs below all the LOCs. Page 76 of 206 The acute risk quotients for multiple applications to turf exceed all LOCs for all weight classes of mammals foraging on short grass and small insects. These RQs range from 0.16 to 0.77. The acute RQs for single applications are restricted to 15 and 35 g mammals foraging in short grass and range from 0.1 to 0.3. Mammalian dietary based chronic RQs exceed the chronic LOCs only for multiple applications to turf and range from 1.3 to 2.6 for mammals foraging in short grass, tall grass, and broadleaf forage, and small insects. However, the dose based RQs exceed the chronic LOC for herbivore/ insectivore mammals foraging in all food categories in all weight classes with the exception of 1000 g mammals foraging in the fruit/ pods/ large insect food category. These RQs range from 3.3 to 13.

Terrestrial Plants Risk quotients for terrestrial plants exceed the LOC for barley, rye, triticale, stone fruit, wheat, corn, celery, grasses grown for seed, rice, wild rice, and turf use sites. These RQs range from 1.0 to 16.2.

2. Probit Dose Response Relationship Because screening level acute LOCs are exceeded for Acute Risk, Restricted Use and Acute Listed Species for freshwater fish, aquatic plants, birds, mammals, and terrestrial plants, the Agency uses the dose response relationship from the toxicity study used for calculating the RQ to estimate the probability of acute effects associated with an exposure equivalent to the EEC. This information serves as a guide to establish the need for and extent of additional analysis that may be performed using Services provided " species profiles" as well as evaluations of the geographical and temporal nature of the exposure to ascertain if a " not likely to adversely affect" determination can be made. The degree to which additional analyses are performed is commensurate with the predicted probability of adverse effects from the comparison of the dose response information with the EECs. The greater the probability that exposures will produce effects on a taxa, the greater the concern for potential indirect effects for listed species dependant upon that taxa, and therefore, the more intensive the analysis on the potential listed species of concern, their locations relative to the use site, and information regarding the use scenario ( e. g., timing, frequency, and geographical extent of pesticide application).

The Agency uses the probit dose response relationship as a tool for providing additional information on the listed animal species acute levels of concern. The acute Listed Species LOCs of 0.1 and 0.05 are used for terrestrial and aquatic animals, respectively. As part of the risk characterization, an interpretation of acute LOCs for listed species is discussed. This interpretation is presented in terms of the chance of an individual event ( i. e., mortality or immobilization) should exposure at the estimated environmental concentration actually occur for a species with sensitivity to propiconazole on par with the acute toxicity endpoint selected for RQ calculation. To accomplish this interpretation, the Agency uses the slope of the dose response relationship available from the toxicity study used to establish the acute toxicity measurement endpoints for each taxonomic group. The individual effects probability associated with the LOCs is based on the mean estimate of the slope and an assumption of a probit dose response relationship. In addition to a single effects probability estimate based on the mean, upper and lower estimates of the effects, probabilities are also provided to account for variance Page 77 of 206 in the slope. The upper and lower bounds of the effects probability are based on available information on the 95% confidence interval of the slope. Confidence in the applicability of the assumed probit dose response relationship for predicting individual event probabilities is also relevant. Studies with good probit fit characteristics ( i. e., statistically appropriate for the data set) are associated with a high degree of confidence. Conversely, a low degree of confidence is associated with data from studies that do not statistically support a probit dose response relationship. In addition, confidence in the data set may be reduced by high variance in the slope estimate ( i. e., large 95% confidence intervals), despite good probit fit characteristics.

For fish, aquatic invertebrates, birds, and mammals, the individual effect probabilities were calculated based on an Excel spreadsheet tool IECV1.1 ( Individual Effect Chance Model Version 1.1) developed by U. S. EPA, OPP, Environmental Fate and Effects Division ( June 22, 2004). The model allows for such calculations by entering the mean slope estimate ( and the 95% confidence bounds of that estimate) as the slope parameter for the spreadsheet.

With regard to birds and the calculation of the chance of an individual event occurrence associated with an LOC of 0.1 is based on an assumption of a probit dose response relationship with a mean estimated slope of 4.1 ( MRID 00079689). The corresponding estimated chance of individual mortality associated with the listed species LOC of 0.1 the acute toxic endpoint for birds is 1 in 4.84 x 103. It is recognized that extrapolation of very low probability events is associated with considerable uncertainty in the resulting estimates. To explore possible bounds to such estimates, the upper and lower values for the mean slope the estimated the 95% confidence intervals of 0.72 and 7.48 were used to calculate upper and lower estimates of the effects probability associated with the listed species LOC. These values are 1 in 4.24 and 1 in 2.67 x1013, respectively. Since acute RQs exceed the levels of concern up to 0.7 for 20 g birds foraging in short grass the probabilities of occurrences can be as high as 1 in 3.8 for these birds.

These same calculations from the adjusted mammalian LD50 of 729 mg/ kg bw and a default mean slope of 4.5 estimate the chance of individual mortality associated with the listed species LOC of 0.1 is 1 in 2.94 x 105.

The slope for the most sensitive freshwater fish DER is 7.28 with upper and lower bound confidence limits of 2.27 and 12.28 ( MRID 0067923). The chance of an individual event occurrence associated with a LOC of 0.05 and a LC50 of 846 µ g/ L is 1 in 1 x 105, the limit of Excel reporting. Since the highest freshwater fish LOC is 0.05, it is unlikely that a slope of 7.28 with will result in a high probability of occurrence for this maximum LOC of 0.05. The 95% confidence limit occurrences are 1 in 864 and 1 in 1 x 1016.

The most sensitive marine/ estuarine eastern oyster slope was 3.35 with confidence limits of 2.89 and 3.83 and a LC50 of 113 µ g a. i./ L ( MRID 132933). The chance of an individual event occurrence associated with a LOC of 0.05 and a LC50 of 113 µ g/ L is 1 in 1 x 105. The 95% confidence limit occurrences are 1.18 in 104 and 3.19 x 106.

3. Data Related to Under represented Taxa Page 78 of 206 Although the Level I screening assessment process relies on RQ calculations that use toxicity endpoints selected from the most sensitive species tested within broad taxonomic groups, there may be situations in which additional effects data from one or more sources may suggest that a given suite of listed taxa may be more or less sensitive than suggested by the effects data used for RQ calculations. In these circumstances, the screening level RQs are not changed, but effects data more specific to listed species may be used to evaluate the extent to which screening level RQs adequately represent conclusions regarding effects on specific listed taxa. An example of this is illustrated in the analysis for listed amphibians. Fish effects data are commonly used to evaluate impacts to aquatic phase amphibians at the screening level. But, if toxicity data were available on amphibians, and they were markedly different from the surrogate fish data used to estimate RQs, these effects data may be compared with estimated exposures for the following purposes:

° Determine our level of confidence in the ability of listed species conclusions based on the fish based RQs to provide appropriate protection for listed amphibians, and to ° More fully discuss any concerns for listed amphibians.

With regard to available toxicity data for propiconazole, data are available for the estuarine/ marine mollusc. The LC50 of 113 µ g a. i./ L indicates that propiconazole is highly toxic to mollusks and this value can be applied as a potential surrogate species for freshwater mollusks. Since this mollusk value is the most sensitive species tested and was already used to calculate RQs for estuarine/ marine invertebrates, risk to listed mollusks can be assumed for all applications to turf.

4. Implications of Sub lethal Effects The Level I screening assessment relies on the acute mortality endpoint as well as a suite of sub lethal responses to the chemical stressor, as determined by the testing of species response to chronic exposure conditions and subsequent chronic risk assessment.

Examples of these sub lethal endpoints include the following:

Aquatic Organisms Test Type Sub lethal Measures of Effect Invertebrate Life Cycle Production of young by first generation Length of first generation Fish Early Life Stage Embryo hatch rate Time to hatch Time to swim up Growth ( length and weight) Pathological or histological effects Observations of other clinical signs Fish Life Cycle Embryo hatch rate Time to hatch Page 79 of 206 Growth ( length) Exposed adult egg production Second generation hatch rate Second generation growth Birds Reproduction Maternal weight Eggs laid/ hen Eggs cracked Eggshell thickness Viable embryos Hatchling number 14 day survivors Gross necropsy ( organ lesions, fat and muscle deterioration) Observations of other clinical signs Mammals Two Generation Total panel of reproduction parameters including: Reproduction histopathology, parental and offspring growth, weight, mating, lactation, gonadal development milestones, sexual organ performance, and offspring production The dietary based chronic risk quotients, which are presented in detail in Appendix XX, show that chronic levels of concern are exceeded for birds for multiple applications of propiconazole to turf use sites when the NOAEL of 1000 mg/ kg diet is used to assess chronic risk. In addition, mammalian dietary based chronic RQs exceed the chronic LOC only for multiple applications to turf use sites and range from 1.3 to 2.6 for mammals foraging in short grass, tall grass, and broadleaf forage, and small insects. However, the dose based RQs exceed the chronic LOC for herbivore/ insectivore mammals foraging in all food categories in all weight classes with the exception of 1000 g mammals foraging in the fruit/ pods/ large insect food category. These RQs range from 1.2 to 13.

c. Indirect Effects Analysis In conducting a screen for indirect effects, direct effect LOCs for each taxonomic group are used to make inferences concerning the potential for indirect effects upon listed species that rely upon non listed organisms in these taxonomic groups as resources critical to their life cycle. Pesticide use scenarios, resulting in RQs that are below all direct effect listed species LOCs for all taxonomic groups assessed are considered of no concern for risks to listed species either by direct or indirect effects. However, there may be situations where a taxonomic group is not quantitatively assessed ( e. g., terrestrial insects), but other lines of evidence are sufficiently supportive of concerns for indirect effects on listed organisms that are dependant upon that taxonomic group.

The Level I screening indirect effects analysis documents those types of dependencies upon non listed organisms that could be important sources of indirect effects to listed organisms Page 80 of 206 should effective levels of the pesticide coincide with locations of listed species and the biologically based resources upon which they depend. Generally speaking, when a taxonomic group shows a RQ higher than the listed species LOC, a potential concern for indirect effects to any listed species in any taxonomic group that has a dependency on the taxa for which the RQ is in excess of the LOC and which is co located with the pesticide use site is established.

For listed species LOCs for animals, the RQs vary with the slope of the dose response relationship. So, when an RQ for an animal taxonomic group exceeds the listed species LOC, one is concerned for a potential for indirect effects in any listed species in any taxonomic group that is co located with the pesticide use site. This information serves as a guide to establish the need for and extent of additional analysis that may be performed using Services provided " species profiles" as well as evaluations of the geographical and temporal nature of the exposure to ascertain if a " not likely to adversely affect" determination can be made. The degree to which additional analyses are performed is commensurate with the predicted probability of adverse effects from the comparison of dose response information with the EECs. The greater the probability that exposures will produce effects on a taxa, the greater the concern for potential indirect effects for listed species dependant upon that taxa, and therefore, the more intensive the analysis on the potential listed species of concern, their locations relative to the use site, and information regarding the use scenario ( e. g., timing, frequency, and geographical extent of pesticide application). Greatest concerns would exist when exposure is associated with a risk higher than the effects probability associated with the non listed LOC for a pesticide with an average slope of 4.5.

The average slopes for birds and mammals are 4.1 and 4.5, respectively. As discussed above in the Probit Dose Response Relationship section, these slopes represent an estimated chance of individual listed species mortality of 1 in 1.84 x 103 for birds and 1 in 2.94 x 105 for mammals and. Although this probability is less than the probability of a slope of 4.5, the lower bounds of these slopes are 1 in 4.24 for birds.

Listed species LOCs for propiconazole are exceeded for herbivore/ insectivorous mammals, birds, aquatic and terrestrial plants, and listed freshwater fish and estuarine/ marine invertebrates for use on turf. In addition, RQs for the use on rice exceed the freshwater and estuarine/ marine plants LOCs, based on toxicity to freshwater and marine diatoms. This means that there are potential concerns for indirect effect on animals that eat birds, mammals, fish, or estuarine/ marine aquatic invertebrates; plants that require mammals, birds, or insects as pollinators or seed dispersers; and listed animals that use mammal or reptile burrows for shelter or breeding habitat.

d. Critical Habitat In the evaluation of pesticide effects on designated critical habitat, consideration is given to the physical and biological features ( constituent elements) of a critical habitat identified by the U. S Fish and Wildlife and National Marine Fisheries Services as essential to the conservation of a listed species and which may require special management considerations or protection. The evaluation of impacts for a screening level pesticide risk assessment focuses on the biological features that are constituent elements and is accomplished using the screening level taxonomic Page 81 of 206 analysis ( risk quotients, RQs) and listed species levels of concern ( LOCs) that are used to evaluate direct and indirect effects to listed organisms.

The screening level risk assessment has identified potential concerns for indirect effects on listed species for those organisms dependant upon mammals, birds, aquatic and terrestrial plants, and estuarine/ marine fish and invertebrates. In light of the potential for indirect effects, the next step for EPA and the Service( s) is to identify which listed species and critical habitat is potentially implicated. Analytically, the identification of such species and critical habitat can occur in either of two ways. First, the agencies could determine whether the action area overlaps critical habitat or the occupied range of any listed species. If so, EPA would examine whether the pesticide's potential impacts on non listed species would affect the listed species indirectly or directly affect a constituent element of the critical habitat. Alternatively, the agencies could determine which listed species depend on biological resources, or have constituent elements that fall into, the taxa that may be directly or indirectly impacted by the pesticide. Then EPA would determine whether use of the pesticide overlaps the critical habitat or the occupied range of those listed species. At present, the information reviewed by EPA does not permit use of either analytical approach to make a definitive identification of species that are potentially impacted indirectly or critical habitats that is potentially impacted directly by the use of the pesticide. EPA and the Service( s) are working together to conduct the necessary analysis.

This screening level risk assessment for critical habitat provides a listing of potential biological features that, if they are constituent elements of one or more critical habitats, would be of potential concern. These correspond to the taxa identified above as being of potential concern for indirect effects and include the following: mammals, birds, aquatic and terrestrial plants, and estuarine/ marine fish and invertebrates. This list should serve as an initial step in problem formulation for further assessment of critical habitat impacts outlined above, should additional work be necessary.

e. Co occurrence Analysis The goal of the analysis for co location is to determine whether sites of pesticide use are geographically associated with known locations of listed species. At the screening level, this analysis is accomplished using the LOCATES database. The database uses location information for listed species at the county level and compares it to agricultural census data for crop production at the same county level of resolution. The product is a listing of federally listed species that are located within counties known to produce the crop upon which the pesticide will be used. Because the Level I screening assessment considers both direct and indirect effects across generic taxonomic groupings, it is not possible to exclude any taxonomic group from a LOCATES database run for a screening risk assessment. The complete results are listed in Appendix X. However, it must be noted that the LOCATES database is currently unable to correlate the locations of listed species with turf use sites, and since the turf use site represents the greatest potential risk to listed species, there is a great uncertainty in the evaluation of listed species associated with the use of propiconazole. This assessment consequently only deals with the use sites for which data have direct association vis à vis the LOCATES database. Therefore, the use sites represented in the report include corn, celery, rice, barley, rye, triticale, stone fruit, and grasses grown for seed. Page 82 of 206 Although this list is repetitive because it lists the species within each county, this list could be refined by consideration of the biology of listed species, the locations of these species, fate and transport properties of the chemical, and the locations of use sites. In the case of propiconazole, the possible reduction of use rates and/ or number of applications could shorten the list significantly.

C. Description of Assumptions, Limitations, Uncertainties, Strengths and Data Gaps The results of the risk assessment suggest a limited concern for avian acute or chronic risks to non listed species.

There are a number of areas of uncertainty in the avian risk assessment that merit discussion. These include the following:

1. Only dietary exposure is included in the exposure assessment. Other exposure routes are possible for birds in treated areas. These routes include ingestion of contaminated soils, ingestion of contaminated drinking water, preening, dermal contact, and inhalation. Consumption of drinking water would appear to be inconsequential if water concentrations were equivalent to the low concentrations from PRZM/ EXAMS. However, direct application to puddles or to dew on plant surfaces could be expected to be higher, and so the drinking water route remains an unquantified concern. Finally, preening exposures, involving the oral ingestion of material preened from the feathers, remains an unquantified but potentially important exposure route.

2. The risk assessment only considers the most sensitive species tested. Avian acute and chronic risks are based on toxicity data for the most sensitive bird species tested. Bird responses to a toxicant can be expected to be variable across species. In the case of propiconazole additional species tested were not tested to high enough levels to determine a definitive LC50. The position of the two tested species relative to the distribution of all species' sensitivities to propiconazole is unknown.

3. The risk assessment assumes 100% of the avian diet is relegated to single food types foraged only from treated fields. These assumptions are likely to be conservative for many species. The assumption of 100% diet from a treated area may be realistic for acute exposures, but long term exposures modeled as single food types composed entirely of material from a treated field is uncertain.

4. The exposure assessment used 95th percentile residue values. The residue values used from Fletcher et al. ( 1994) represent values that ensure 5% or less of the residue measurements included in the study are greater ( i. e. a 95th percentile). Values selected from points lower on the distribution would yield lower exposure estimates and lower resultant RQs. Page 83 of 206 The risk quotient calculations suggest limited concern for acute risks in populations of small mammals. In the case of small insectivorous/ herbivorous mammals in treated areas, the risk quotients suggest that restricted use provisions on the label could reduce these concerns.

There are additional concerns for reproduction/ developmental effects. Reproduction/ developmental risks are of concern in one or more food items for all labeled crops. However, the types of effects observed in dietary developmental/ reproduction studies have uncertain implications for wild mammals.

LITERATURE CITED Exposure Analysis Modeling System ( EXAMS): User Manual and System Documentation. Ecosystem Research Division, National Exposure Research Laboratory. U. S. Environmental Protection Agency, Athens, GA Carsel, R. F., J. C. Imhoff, P. R. Humel, J. M. Cheplick, and A. S. Donigian, Jr. 1997. PRZM 3, A Model for Predicting Pesticide and Nitrogen Fate in the Crop Root and Unsaturated Zones: User's Manual for Release 3.0. National Exposure Research Laboratory, Office of Research and Development, U. S. Environmental Protection Agency, Athens, GA.

Environmental Fate and Effects Division. 2002. Guidance for Selecting Input Parameters in Modeling the Environmental Fate and Transport of Pesticides, Version II. U. S. Environmental Protection Agency. Washington, D. C. http:// www. epa. gov/ oppefed1/ models/ water/ input_ guidance2_ 28_ 02. htm Gianessi, L. P. and M. B. Marcelli. 2000. Pesticide Use in U. S. Crop Production: 1997 National Summary Report. National Center for Food and Agricultural Policy, Washington D. C. http:// www. ncfap. org/ database/ default. htm Hoerger, F., and E. E. Kenaga. 1972. Pesticide residues on plants: Correlation of representative data as a basis for estimation of their magnitude in the environment. In F. Coulston and F. Korte, eds., Environmental Quality and Safety: Chemistry, Toxicology, and Technology, Georg Thieme Publ, Stuttgart, West Germany, pp. 9 28.

Iwasa, Takao. et al., 2003. Mechanism for the differential toxicity of neonicotinoid insecticides in the honey bee, Apis mellifera. Crop Protection 23 ( 2004) 371  378.

Levine, S. L. and Oris, James T. 1999. Enhancement of Acute Parathion Toxicity to Fathead Minnows Following Pre exposure to Propiconazole. Pesticide Biochemistry and Physiology 65, 102  109.

OPP EFED. 1999. Downwind Deposition Tolerance Bounds for Orchards. Scientific Advisory Panel background document. http:// www. epa. gov/ scipoly/ sap/ 1999/ july/ airblast. pdf. Page 84 of 206 Ronis, M. J. and Badger, T. M. 1994. Toxic Interactions between Fungicides that Inhibit Ergosterl Biosynthesis and Phosphorothioate Insecticides in the Male Rat and Bobwhite Quail ( Colinus virginianus). Toxicology and Applied Pharmacology 130, pp. 221   228.

Teske, M., S. L. Bird, D. M. Esterly, S. L. Ray, and S. G. Perry. 2001. A User's Guide for AgDRIFT 2.01: A Tiered Approach for the Assessment of Spray Drift of Pesticides. Spray Drift Task Force. Macon, MO.

Thelin, G. P and L. P Gianessi. 2000. Method for Estimating Pesticide Use for County Areas of the Conterminous United States. U. S. GEOLOGICAL SURVEY. Open File Report 00 250. Sacramento, CA. http:// ca. water. usgs. gov/ pnsp/ pesticide_ use_ maps_ 1997/

U. S. EPA. 2004. Overview of the Ecological Risk Assessment Process in the Office of Pesticide Programs. Office of Prevention, Pesticides and Toxic Substances. Office of Pesticides Programs. Washington, DC. January 23, 2004.

U. S. EPA. 1998. Guidelines for Ecological Risk Assessment. Risk Assessment Forum, Washington, DC. EPA 630/ R 95/ 002F April 1998.

Walker, C. H. 1998. Avian forms of cytochrome P450. Comparative Biochemistry and Physiology Part C 121 ( 1998) 65  72.

Willis, G. H., and L. L. McDowell. 1987. Pesticide Persistence on Foliage in Reviews of Environmental Contamination and Toxicology. 100: 23 73. Page 85 of 206 Appendix A   Environmental Fate Discussion Propiconazole [ 1[[ 2( 2,4 dichlorophenyl) 4 propyl 1,3 dioxolan 2 yl] methyl] 1H 1,2,4 triazole] is a systemic broad spectrum fungicide registered for treatment of disease in bananas, barley, celery, corn ( field, pop, and sweet), grasses grown for seed, mint, oats, peanuts, pineapple, plantains, rice and wild rice, rye, stone fruits, sugarcane, and wheat.

Empirical Formula: C15H17Cl2N3O2 Molecular Weight: 342.23 CAS Registry No.: 60207 90 1 PC Code: 122101 Trade Name Banner, Orbit, Tilt Mode of Action Sterol biosynthesis ( ergosterol biosynthesis) inhibitor Systemic foliar fungicide with protective and curative action Acropetal xylem translocation Formulation Emulsifier Concentrate, Flowable Concentrate, Liquid, Liquid Ready To Use, Soluble Concentrate/ Liquid, Wettable Powder Product Chemistry Propiconazole is an amber to yellow viscous liquid with a boiling point of 95 C, density of 1.27 g/ cm3, octanol/ water partition coefficient ( log Kow) of 2.95, and vapor pressure of 1.0 x 10 6 Torr at 20 C. Propiconazole is slightly soluble in water ( 110 ppm at 20 C), practically insoluble in hexane ( 0.06 ppm), and is miscible with most organic solvents, including methanol, isopropanol, acetone, methylene chloride, toluene, and n octanol. Cl Cl O O N N N CH 3 OH Page 86 of 206 Environmental Fate Summary Propiconazole appears to be persistent and moderately mobile to relative immobile in most soil and aqueous environments. For aquatic environment, propiconazole degradation appears to be dependent solely on aqueous photolysis in the presence of photo sensitizers. In soil environment, propiconazole dissipation appears to be depending on incorporation or binging into soil organic matter content.

Laboratory and terrestrial field dissipation data indicate that propiconazole is stable in soil and aqueous environments. Propiconazole was stable to hydrolysis ( t ½ > 30 days), aqueous photolysis (< 10% of applied degraded in 30 days), soil photolysis (< 8% of applied degraded in 30 days), aerobic aquatic metabolism ( t ½ > 30 days), aerobic soil metabolism ( t ½ = 30 to 112 days), and anaerobic aquatic metabolism ( t ½ = 363 days). The terrestrial field dissipation data were consistent with reported half lives of > 100 days for four soil textures. However, in supplemental aquatic dissipation data using basin irrigation and flow through irrigation systems in rice fields, propiconazole was found to be dissipating rapidly ( t ½ < 5 days). Aqueous photolysis studies using sensitizers indicated rapid degradation ( t ½ < 1 days) of propiconazole, which appears to be the case in rice field. Furthermore, aquatic metabolism and dissipation studies indicate propiconazole dissipates by incorporation or binding into the organic matter content of soil/ sediment.

Propiconazole mobility in soil appears to be dependent on the soil's organic matter content. In general, propiconazole appears to be moderately mobile ( Kd < 5) in soils with a low organic matter content (< 1%). However, in soils with higher organic matter content (> 1%), propiconazole appears to be relatively immobile ( Kd > 5). Therefore, propiconazole may reach ground water in soils with low organic contents. More importantly, propiconazole may contaminate surface water through off site runoff and spray drift.

161 1 Hydrolysis ( MRID: 00067901 / 42238201)

Propiconazole appears to be stable (< 5% degradation) to hydrolysis in aqueous buffered solutions at pH 5, 7, and 9. The studies were conducted at 70oC with a concentration of 10 ppm. The mean value of the recovered propiconazole as parent in test samples was 100 ± 3.1%.

161 2 Photodegradation in Water ( MRID: 41811901)

Phenyl ring labeled [ 14C] propiconazole photodegraded slowly (  10% of applied radioactivity) in an aqueous pH 7 solution exposed to an intermittent ( 12 light on/ 12 light off) artificial light ( xenon lamp) source for 30 days at 25 oC. There were no major degradates in either the light exposed or dark controls. Four unidentified degradates were detected in the light exposed samples at   3.4% (  0.37 ppm) of the recovered.

161 3 Photodegradation on Soil ( MRID: 41811902) Page 87 of 206 Phenyl ring labeled [ 14C] propiconazole photodegraded slowly (<  8 % of applied radioactivity) on sandy loam soil expososed to an intermittent ( 12 light on/ 12 light off) artificial light ( xenon lamp) source for 30 days at 25 oC. In the light samples, two degradates, 1( 2,4 dichlorophenyl) 2( 1H 1,2,4 triazol 1 yl) ethanone ( CGA 91304) and 1( 2,4 dichlorophenyl) 1H 1,2,4 triazole 1 ethanol ( CGA 91305) were identified at concentrations < 10% of applied radioactivity.

162 1 Aerobic Soil Metabolism ( MRID: 129912)

The degradation of the fungicide CGA 64250 was studied at a concentration of 1 ppm in a silty loam soil ( sand 33.5%, silt 61.7%, clay 4.8%, organic carbon 2.7%, pH 7.6) under aerobic, aerobic/ anaerobic and sterile/ aerobic conditions. CGA 64250 disappeared in the aerobic experiment with a half life of 70 days and was not significantly degraded under the anaerobic and sterile/ aerobic conditions. Most of the material became bound to soil. The metabolite CGA 118245 accounted for 23.6% of the 14C after 52 weeks of aerobic conditions. The metabolite CGA 136735 reached a maximum amount of 22.2% after 12 weeks aerobic incubation, which decreased thereafter to 5.4% after 52 weeks.

162 1 Aerobic Soil Metabolism ( MRID: 129914)

The degradation of the propiconazole was studied in a silty loam with 14C dioxolane and 14Cphenylring labeled CGA 64250. The half life values are 43 days and 47 days, respectively. The main metabolite found in both experiments was 14CO2. Its amount increased steadily during the experiments reaching values of 42.0 and 45.8% of the applied radioactively for 14C dioxolane and 14C phenylring CGA 64250, respectively, after 168 days of aerobic incubation. This indicated that both dioxolane and the phenylring moieties are mineralized at about the same rate by soil microorganisms. The metabolite CGA 136735 reached a maximum amount of 13.8 and 16.9% of the dose applied after 24 days with the 14C dioxolane and the 14C phenylring labeled materials, respectively.

162 3 Anaerobic Aquatic Metabolism ( MRID: 42347902)

Propiconazole had a calculated half life of 363 days when applied to an aquatic sediment system and incubated under anaerobic conditions. However, degradation appeared to slow down after the first 30 days indicating a biphasic degradation of propiconazole. The half life calculation reported was based on the linear ( kinetic) phase of the study ( 0 to 30 days post treatment period). In addition, propiconazole appears to readily bind to soil/ sediment. As radioactivity in the water phase dropped from an initial concentration of 93.2% to 3.1% of applied at day 360 posttreatment the radioactivity in the soil extracts increased from an initial concentration of 6.7% to 89.3% of applied at day 360 post treatment.

162 4 Aerobic Aquatic Metabolism ( MRID: 42347901)

Propiconazole had an extrapolated half life of >> 30 days when incubated under aerobic aquatic ( sediment) conditions. The total concentration ( in water and sediment) of parent propiconazole declined from an initial value of 94.6% to 88.79% by 30 day post treatment. Propiconazole did Page 88 of 206 appear to readily bind to soil/ sediment, as well. As the radioactivity in the aqueous phase dropped from an initial concentration of 92.8% to 10.0% of applied at 30 day post treatment, the radioactivity in the soil extracts increased from an initial concentrations of 6.5% to 84.7% at 30 day post treatment.

163 1 Column Leaching and Adosprtion/ desorption ( MRID: 67906)

14C CGA 64250 was applied to the top of a 30 cm soil column at a rate equivalent to 5 kg/ ha. Two hundred mm of water were applied over a 2 day period. Four different types of soil were used in this study: sand, loamy sand, sandy clay loam and loam. The study demonstrates that CGA 64250 is capable of leaching through sandy soil, which is low in organic matter.

163 1 Column Leaching and Adosprtion/ desorption ( MRID: 67907)

14C CGA 64250 was applied to loamy sand and loam soils and the mixture was aged aerobically for 30 days at 25oC. Two cm layer of the treated soils were placed on top of 28 cm columns of untreated soils, which were eluted daily with 16 ml of water for 45 days. The leaching of aged residues of CGA 64250 was minimal.

163 1 Column Leaching and Adosprtion/ desorption ( MRID: 41727001)

The adsorption Kd values were 1.2, 2.81, 4.49, 8.88 and 9.34, respectively for Plainfield sand, Mississippi silt loam, California sandy loam, Hagerstown silty clay loam, and Arizona silty clay loam. The Koc values calculated for each soil was 685, 436, 382, 604, and 1134.

The desorption Kd values were 1.57 ( Plainfield sand), 3.00 ( Mississippi silt loam), 5.35 ( California sandy loam), 10.3 ( Hagerstown silty clay loam), and 10.1 ( Arizona silty clay loam). The desorption Kd value was greater than the adsorption Kd for all the soils. The Koc values were 893, 464, 455, 703, and 1229, respectively for the above soils.

163 1 Column Leaching and Adosprtion/ desorption ( MRID: 44701801)

This aged leaching study is scientifically valid and provides useful information on the soil mobility of propiconazole in four soils. However, due to the relative long aerobic soil metabolism half life ( 288 days to 3.2 years as reported in the study for four soils and 60 84 days fro silt loam as reported in MRID 67908 and MRID 133376), the incubation period of 30 days prior to column leaching did not provide sufficient information on the mobility of propiconazole degradates.

The soil mobility of triazole ring labelled propiconazole, applied at nominal rate of 1.8 ppm ( equivalent to the recommended maximum application rate of 1.8 lb a. i./ acre applied with 0" to 3" soil incorporations) and aged ( 30 days), was studied in sand, sandy loam, silty loam, and clay soil columns which were leached with 0.01 M CaCl2 solution over # 25 hours. Total [ 14C] residues in the leachate were 2.5%, 2.9%, 5.8% and 2.9% of the applied radioactivity, respectively for sand, sandy loam, silt loam and clay loam soil columns. Page 89 of 206 164 1 Terrestrial Field Dissipation ( MRID: 45528701, 45528702)

Soil dissipation/ accumulation of cis trans 1[ 2( 2,4 dichlorophenyl) 4 propyl 1,3 dioxolan 2 ylmethyl] 1H 1,2,4 triazole ( propiconazole; CGA 64250) under U. S. field conditions was conducted in a bare plot and a turf plot of sandy loam soil in California. Propiconazole was broadcast sprayed four times ( at 21 day intervals) to both test plots at a target application rate of 1.98 kg a. i./ ha/ application ( 1.77 lb a. i./ A/ application) in separate bare ground and turf test plots measuring approximately 90 x 6 m that were each divided into three subplots for sampling. The test substance was applied at 100% of the proposed maximum label rate. Rainfall was supplemented with irrigation to reach 450% of the 10 year average rainfall during the study period.

Soil samples were taken prior to and following each application and at 1, 3, 7, 14, 30, 60, 90, 120, 180, 270, 360, 450, and 540 days following the fourth application to a depth of 0 120 cm in both the bare ground and turf plots. Grass and thatch samples were also collected from the turf plot at each sampling interval. Soil samples were reflux extracted with 70% methanol: deionized water, passed through a SAX SPE column, and then applied to an ENV SPE column attached on top of a SCX SPE column. The SPE columns were disconnected and eluted separately for propiconazole, CGA 217495, CGA 91305, CGA 71019, and Hydroxy Isomers, CGA 118244, CGA 118245, and CGA 136735. Samples collected from the bare plot were analyzed following up to a maximum of 216 days of storage. Samples collected from the turf plot were analyzed following up to a maximum of 217 days of storage. The LOQ was 5.0 ppb for all analytes in soil. Grass samples were extracted by shaking with acetone and were analyzed for propiconazole using LC/ MS/ MS. The LOQ was 50 ppb.

In the bare plot, propiconazole was detected in the 0 15 cm soil depth at 463 ppb following the first application, 696 ppb following the second application, 1256 ppb following the third application, and a maximum of 1556 ppb at 3 days following the fourth application. Following the fourth application, propiconazole decreased to 687 ppb by 120 days and 313 ppb by 270 days, and was 75.4 ppb at 540 days post treatment, the last sampling interval. Propiconazole was detected sporadically in the 15 30 cm soil depth, and was not detected below the 30 45 cm soil depth. The major transformation products detected were CGA 217495, CGA 91305, and CGA 71019. CGA 217495 was initially detected in the 0 15 cm soil depth at 20.6 ppb prior to the second application, increased to a maximum of 254 ppb at 90 days after the fourth application, and decreased to 60.3 ppb by 540 days. CGA 217495 was detected in the 15 30 cm, 30 45 cm, and 45 60 cm depths at maximum concentrations of 37.5 ppb ( 270 days), 16.8 ppb ( 270 days), and 10.1 ppb ( 120 days), respectively. CGA 91305 was initially detected in the 0 15 cm soil depth at 6.53 ppb prior to the second application, increased to a maximum of 48.0 ppb at 90 days after the fourth application, and decreased to 11.7 ppb by 540 days. CGA 91305 was detected in the 15 30 cm and 30 45 cm depths at maximum concentrations of 11.0 ppb ( 270 days) and 6.0 ppb ( 270 days), respectively. CGA 71019 was initially detected in the 0 15 cm soil depth at 5.13 ppb prior to the second application, increased to a maximum of 87.5 ppb at 90 days after the fourth application, and decreased to 21.5 ppb by 540 days. CGA 71019 was detected in the 15 30 cm, 30 45 cm, and 45 60 cm depths at maximum concentrations of 14.6 ppb ( 270 days), 12.2 ppb ( 360 days), and 11.9 ppb ( 360 days), respectively. Page 90 of 206 Under field conditions in the bare plot, the total carryover of residues of propiconazole and its transformation products was 4.8% and 8.3% of the maximum propiconazole detection in soil ( 1556 ppb), respectively, at the end of the study period, 540 days after the fourth application.

In the turf plot, propiconazole was detected below the thatch in the 7.5 15 cm soil depth twice, at 50.3 ppb at 1 day, and 11.4 ppb at 7 days after the last application, and was detected once in the 15 30 cm depth. Propiconazole was detected in the grass at 93542 ppb following the first application, 60717 ppb following the second application, 64492 ppb following the third application, and 70867 ppb following the fourth application. Following the fourth application, propiconazole decreased to 33533 ppb by 3 days, 7000 ppb by 30 days, and was last detected at 352.3 ppb at 120 days post treatment. Propiconazole was detected in the 0 7.5 cm thatch layer at a maximum of 541 ppb at 7 days after the fourth application, decreased to 101 177 ppb by 14 90 days, and was detected at 11.9 ppb at 540 days post treatment, the last sampling interval. The major transformation products detected in soil ( defined as detection > 10 ppb) were CGA 217495 and CGA 71019. CGA 217495 was detected sporadically in the 7.5 15 cm soil depth at concentrations up to 6.5 ppb ( 120 days), and was detected once each in the 15 30 cm and 30 45 cm soil depths at concentrations of 11.1 ppb and 5.5 ppb, respectively, at 180 days. CGA 71019 was detected in the 7.5 15 cm, 15 30 cm, 30 45 cm, and 45 60 cm soil depths at maximum concentrations of 22.4 ppb ( 90 days), 8.2 ppb ( 180 days), 6.0 ppb ( 180 days), and 9.9 ppb ( 360 days), respectively. The major transformation products detected in thatch were CGA 217495, CGA 91305, and CGA 71019. CGA 217495 was initially detected in the 0 7.5 cm thatch layer at 30.0 ppb prior to the second application, increased to a maximum of 155 ppb at 60 days after the fourth application, and was last detected at 7.7 ppb at 450 days. CGA 91305 was initially detected in the 0 7.5 cm thatch layer at 36.8 ppb prior to the second application, increased to a maximum of 122 ppb at 60 days after the fourth application, and decreased to 5.5 ppb by 540 days. CGA 71019 was initially detected in the 0 7.5 cm thatch layer at 5.4 ppb following the second application, increased to a maximum of 200 ppb prior to the fourth application, and decreased to 18.3 ppb by 540 days.

Under field conditions in the turf plot, the total carryover of residues of propiconazole and its transformation products from thatch was 2.2% and 5.5% of the maximum propiconazole detection in the 0 7.5 cm thatch layer ( 541 ppb), respectively, at the end of the study period, 540 days after the fourth application.

164 1 Terrestrial Field Dissipation ( MRID: 45528703)

Soil dissipation/ accumulation of cis trans 1[ 2( 2,4 dichlorophenyl) 4 propyl 1,3 dioxolan 2 ylmethyl] 1H 1,2,4 triazole ( propiconazole; CGA 64250) under U. S. field conditions was conducted in a bare plot of sandy loam soil in California. Propiconazole was broadcast sprayed four times ( at 7 day intervals) at a target application rate of 0.137 kg a. i./ ha/ application ( 0.122 lb a. i./ A/ application) in a test plot measuring approximately 43 x 24 m that was divided into five sampling zones. The test substance was applied at 110% of the maximum use rate according to the product label. Rainfall was supplemented with irrigation to reach 114% of the target moisture input during the study period. Page 91 of 206 Soil samples were taken prior to and following each application and at 1, 3, 7, 14, 28, 61, 89, 118, 183, 278, 364, 479, and 567 days following the fourth application to a depth of 0 120 cm. Soil samples were reflux extracted with 70% methanol: deionized water, passed through a SAX SPE column, then applied to a ENV SPE column attached on top of a SCX SPE column. The SPE columns were disconnected and eluted separately for propiconazole, CGA 217495, CGA 91305, CGA 71019 and Hydroxy Isomers, CGA 118244, CGA 118245, and CGA 136735. Samples were analyzed following up to 221 days for propiconazole, CGA 217495, CGA 91305, and Hydroxy Isomers, and up to 357 days for CGA 71019. The LOQ was 5.0 ppb for all analytes in soil.

The measured zero time concentration of propiconazole in the 0 15 cm soil depth was 54.7 ppb, which is 90% of the applied rate. Propiconazole was detected in the 0 15 cm soil depth at 75.6 ppb following the second application, 90.7 ppb following the third application, and a maximum of 192.0 ppb following the fourth application. Following the fourth application, propiconazole decreased to 77.2 ppb by 89 days and 51.5 ppb by 118 days, and ranged from 58.3 97.7 ppb from 183 479 days post treatment. Propiconazole was not detected below the 0 15 cm soil depth. The major transformation products detected were CGA 217495 and CGA 91305. CGA 217495 was initially detected in the 0 15 cm soil depth at 5.2 ppb following the fourth application, increased to 10.0 11.1 ppb ( 4.1 4.5% of the total applied propiconazole) from 28 118 days, and decreased to 5.9 ppb by 479 days, the last sampling interval. CGA 91305 was initially detected in the 0 15 cm soil depth at 5.3 ppb following the fourth application and increased to a maximum of 10.6 ppb ( 4.3% of the total applied propiconazole) by 479 days. No transformation products were detected below the 0 15 cm soil depth.

164 2 Aquatic Field Dissipation ( MRID: 452560501)

Propiconazole was reported to dissipate from paddy water and paddy soil (# 2.4 ppb and # 0.13 ppm by Day 28 post treatment of second application, respectively) when aerial applied to rice paddy field plots at Walnut Ridge and Lonoke, Arkansas. However, it appears that only propiconazole was determined in paddy water, paddy soil, and drainage waters. The half lives for propiconazole in paddy water at Walnut Ridge were reported to be 3.4 and 6.1 days for the first and second application, respectively. The half lives for propiconazole in paddy water at Lonoke were reported to be 5.4 and 16.1 days for first and second application, respectively.

Propiconazole detected in storm drainage from the Walnut Ridge and Lonoke plots reached a maximum level of 57 and 97 ppb, respectively. However, at harvest time the drainage water was reported to contain propiconazole at levels of # 0.01 ppb and # 14 ppb for Walnut Ridge and Lonoke sites, respectively.

164 2 Aquatic Field Dissipation ( MRID: 452560502) Propiconazole was reported to dissipate from paddy water and paddy soil (# 13.0 ppb and # 0.02 ppm, respectively) when aerial applied to two rice paddy field plots ( B. C. and M. O.) in Bay City, Texas. However, it appears that only propiconazole was determined in paddy water, paddy soil, and drainage waters. The half lives for propiconazole in paddy water at the B. C. site were reported to be 3.04 and 2.40 days for the first and second application, respectively. The half Page 92 of 206 lives for propiconazole in paddy water at the M. O. site were reported to be 4.58 and 3.22 days for first and second application, respectively.

Propiconazole detected in drainage water from the B. C. and M. O. sites reached a maximum level of 26 and 149 ppb, respectively. However, at harvest time the drainage water was reported to contain propiconazole at levels of # 2.0 ppb and # 9.2 ppb for B. C. and M. O. sites, respectively.

165 4 Accumulation in Fish ( MRID: 40963502)

The bioconcentration factor ( BCF) values are 24X, 138 516X, and 68 203X, respectively for edible, viscera, and whole body of bluegill. The depuration half life is 7 days. Page 93 of 206 Appendix B   Modeling Inputs and Attachments Attachment 1: Input values of PRZM, EXAMS, and SCIGROW Table 1 1. Input Parameters for PRZM with Propiconazole ( version 3.12)

Variable ( units) Variable Description Input Value Source of Info/ Reference DWRATE( 1) 1 ( day 1) Dissolved phase pesticide decay rate in surface horizon DSRATE( 1) 1 ( day 1) Adsorbed phase pesticide decay rate in surface horizon DWRATE( 1) = DSRATE( 1)

The 90th percentile half life value of 69.2 days Aerobic soil metabolism half life values of 70, 43 and 47 days ( MRID: 129912, 129914)

DWRATE( 2) ( day 1) DWRATE( 3) ( day 1) Dissolved phase pesticide decay rate in 1st, and 2nd subsurface horizon DSRATE( 2) ( day 1) DSRATE( 3) ( day 1) Adsorbed phase pesticide decay rate in 1st and 2nd subsurface horizon DWRATE( 2) = DSRATE( 2)

The 90th percentile half life value of 69.2 days DWRATE( 3) = DSRATE( 3)

The 90th percentile half life value of 69.2 days same as above KD( 1) KD( 2) KD( 3) ( cm3 gm 1 or mL g 1 or L kg 1) Pesticide partition or distribution coefficients for each horizon assume average KOC of 648 Mobility  Adsorption/ Desorptio n study : KOC values of 685, 436, 382, 604 and 1134. ( MRID: 41727001)

PLDKRT ( day 1) Foliar decay rate 35 days ( only applicable to foliar applications) default value TAPP ( kg ha 1) Application rate Depending on the labels with the maximum rate and number of applications Product label APPEFF ( decimal) Application efficiency 0.95 for aerial spray; 0.99 for ground spray input guidance document DRFT Spray drift fraction 0.05 for aerial spray; 0.01 for ground spray input guidance document Page 94 of 206 Table 1 2. Input Parameters for EXAMS with Propiconazole ( Version 2.98)

Variable ( units) Variable Description Input Value Source of Info/ Reference HENRY ( atm m3mole 1) Henry's law constant no input, let EXAMS computes KBACW1 ( cfu/ mL) 1 hour 1 Bacterial biolysis in water column 138.4 days 2 x aerobic soil metabolism half life KBACS1 ( cfu/ mL) 1 hour 1 Bacterial biolysis in benthic sediment stable aquatic anaerobic halflife = 363 days ( MRID: 42347902)

KDP ( hour 1) Direct photolysis 0.0 Stable ( MRID: 41811901)

KBH ( mole 1 hour 1) KNH ( hour 1) KAH ( mole 1 hour 1) Base hydrolysis Neutral hydrolysis Acid hydrolysis 0.0 0.0 0.0 Stable ( MRID: 00067901 / 42238201)

KOC ( mL g 1 O. C.) Partition coefficient for organic carbon assume a mean KOC of 648 Mobility  Adsorption/ Desorption study : KOC values of 685, 436, 382, 604 and 1134. ( MRID: 41727001)

MWT ( g mole 1) Molecular weight 342.23 product chemistry SOL ( mg L 1) Aqueous solubility 110 product chemistry QUANT Reaction quantum yield for direct photolysis 1.0 VAPR ( torr) Vapor pressure 1.0 x 10 6 product chemistry Page 95 of 206 Table 1 3. Input Parameters for SCIGROW Variable Description Input Value Soil half life ( day) Aerobic soil metabolism half life values of 70, 43 and 47 days ( MRID: 129912, 129914)

Use the average value of 53 days Pesticide partition or distribution coefficients, Koc KOC values of 685, 436, 382, 604 and 1134. ( MRID: 41727001)*

Use the median value of 604 Application rate Depending on the labels with the maximum rate and number of applications   The Koc value is outside the range of 32  180 mL/ g. Page 96 of 206 Attachment 2: PE4 ( PRZM/ EXAMS) Outputs stored as PPZNDWhE. out Chemical: Propiconazole PRZM environment: NDwheatC. txt modified Satday, 12 October 2002 at 16: 15: 08 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 16: 33: 30 Metfile: w14914. dvf modified Wedday, 3 July 2002 at 09: 05: 52 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 0.7825 0.7691 0.73 0.6742 0.6455 0.3181 1962 1.786 1.752 1.644 1.522 1.46 0.9746 1963 1.975 1.943 1.843 1.685 1.608 1.324 1964 3.484 3.412 3.147 2.719 2.61 1.901 1965 2.448 2.423 2.351 2.277 2.239 2.086 1966 2.324 2.3 2.218 2.125 2.133 1.993 1967 2.301 2.278 2.191 2.068 1.987 1.823 1968 2.064 2.041 1.971 1.864 1.799 1.626 1969 2.891 2.842 2.696 2.451 2.327 1.829 1970 2.616 2.585 2.464 2.242 2.148 2.014 1971 2.333 2.317 2.252 2.153 2.081 2.005 1972 2.243 2.219 2.129 2.053 2.04 1.928 1973 2.177 2.162 2.114 2.069 2.039 1.888 1974 3.35 3.3 3.122 2.88 2.801 2.241 1975 5.028 4.969 4.639 4.174 3.943 3.003 1976 3.231 3.202 3.109 3.082 3.062 2.754 1977 3.693 3.632 3.409 3.092 2.975 2.561 1978 4.03 3.97 3.748 3.433 3.31 2.779 1979 3.218 3.184 3.093 3.034 2.953 2.71 1980 2.819 2.798 2.721 2.654 2.616 2.507 1981 2.69 2.666 2.576 2.507 2.45 2.306 1982 2.421 2.4 2.318 2.238 2.182 2.089 1983 2.694 2.656 2.585 2.454 2.392 2.145 1984 3.105 3.062 2.928 2.691 2.535 2.227 1985 2.645 2.616 2.539 2.455 2.436 2.256 1986 3.228 3.18 3.02 2.824 2.727 2.33 1987 2.502 2.476 2.377 2.313 2.307 2.203 1988 2.295 2.267 2.188 2.107 2.071 1.998 1989 2.522 2.498 2.421 2.297 2.239 2.029 1990 3.157 3.111 2.952 2.687 2.572 2.184 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 5.028 4.969 4.639 4.174 3.943 3.003 0.0645161290322581 4.03 3.97 3.748 3.433 3.31 2.779 0.0967741935483871 3.693 3.632 3.409 3.092 3.062 2.754 0.129032258064516 3.484 3.412 3.147 3.082 2.975 2.71 0.161290322580645 3.35 3.3 3.122 3.034 2.953 2.561 0.193548387096774 3.231 3.202 3.109 2.88 2.801 2.507 0.225806451612903 3.228 3.184 3.093 2.824 2.727 2.33 0.258064516129032 3.218 3.18 3.02 2.719 2.616 2.306 0.290322580645161 3.157 3.111 2.952 2.691 2.61 2.256 0.32258064516129 3.105 3.062 2.928 2.687 2.572 2.241 0.354838709677419 2.891 2.842 2.721 2.654 2.535 2.227 0.387096774193548 2.819 2.798 2.696 2.507 2.45 2.203 Page 97 of 206 0.419354838709677 2.694 2.666 2.585 2.455 2.436 2.184 0.451612903225806 2.69 2.656 2.576 2.454 2.392 2.145 0.483870967741936 2.645 2.616 2.539 2.451 2.327 2.089 0.516129032258065 2.616 2.585 2.464 2.313 2.307 2.086 0.548387096774194 2.522 2.498 2.421 2.297 2.239 2.029 0.580645161290323 2.502 2.476 2.377 2.277 2.239 2.014 0.612903225806452 2.448 2.423 2.351 2.242 2.182 2.005 0.645161290322581 2.421 2.4 2.318 2.238 2.148 1.998 0.67741935483871 2.333 2.317 2.252 2.153 2.133 1.993 0.709677419354839 2.324 2.3 2.218 2.125 2.081 1.928 0.741935483870968 2.301 2.278 2.191 2.107 2.071 1.901 0.774193548387097 2.295 2.267 2.188 2.069 2.04 1.888 0.806451612903226 2.243 2.219 2.129 2.068 2.039 1.829 0.838709677419355 2.177 2.162 2.114 2.053 1.987 1.823 0.870967741935484 2.064 2.041 1.971 1.864 1.799 1.626 0.903225806451613 1.975 1.943 1.843 1.685 1.608 1.324 0.935483870967742 1.786 1.752 1.644 1.522 1.46 0.9746 0.967741935483871 0.7825 0.7691 0.73 0.6742 0.6455 0.3181 0.1 3.6721 3.61 3.3828 3.091 3.0533 2.7496 Average of yearly averages: 2.06772333333333 Inputs generated by pe4. pl  8 August 2003 Data used for this run: Output File: PPZNDWhE Metfile: w14914. dvf PRZM scenario: NDwheatC. txt EXAMS environment file: pond298. exv Chemical Name: Propiconazole Description Variable Name Value Units Comments Molecular weight mwt 342.23 g/ mol Henry's Law Const. henry atm m^ 3/ mol Vapor Pressure vapr 1.0e 6 torr Solubility sol 100 mg/ L Kd Kd mg/ L Koc Koc 648 mg/ L Photolysis half life kdp 0 days Half life Aerobic Aquatic Metabolism kbacw 138.4 days Halfife Anaerobic Aquatic Metabolism kbacs 0 days Halfife Aerobic Soil Metabolism asm 69.2 days Halfife Hydrolysis: pH 7 0 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.125 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 01 06 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 14 days Set to 0 or delete line for single app. Record 17: FILTRA IPSCND 1 UPTKF Record 18: PLVKRT PLDKRT 0.0198 FEXTRC 0.5 Flag for Index Res. Run IR Pond Page 98 of 206 Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

stored as PPZORGsE. out Chemical: Propiconazole PRZM environment: ORgrassseedC. txt modified Satday, 12 October 2002 at 17: 18: 50 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 16: 33: 30 Metfile: w24232. dvf modified Wedday, 3 July 2002 at 09: 06: 10 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.983 1.936 1.767 1.609 1.505 0.8175 1962 2.936 2.887 2.709 2.491 2.355 1.742 1963 4.108 4.05 3.839 3.614 3.484 2.654 1964 4.314 4.26 4.064 3.828 3.687 3.042 1965 4.537 4.497 4.308 4.06 3.912 3.262 1966 4.68 4.624 4.42 4.184 4.044 3.406 1967 4.762 4.703 4.488 4.249 4.105 3.447 1968 4.806 4.749 4.542 4.298 4.149 3.66 1969 5.085 5.029 4.93 4.729 4.58 3.981 1970 5.282 5.221 4.997 4.767 4.61 3.986 1971 5.227 5.172 5.019 4.774 4.619 4.093 1972 5.532 5.472 5.253 5.021 4.852 4.145 1973 5.307 5.25 5.039 4.797 4.648 4.034 1974 5.228 5.169 4.955 4.716 4.574 3.931 1975 5.191 5.135 4.93 4.684 4.541 3.896 1976 5.144 5.09 4.893 4.651 4.506 3.829 1977 5.029 4.971 4.757 4.521 4.38 3.733 1978 5.119 5.056 4.825 4.607 4.461 3.777 1979 5.042 4.985 4.774 4.533 4.384 3.881 1980 5.315 5.264 5.074 4.801 4.647 3.984 1981 5.491 5.429 5.202 4.913 4.74 4.114 1982 5.392 5.331 5.103 4.879 4.728 4.085 1983 5.166 5.11 4.908 4.706 4.574 3.963 1984 5.318 5.26 5.161 4.883 4.711 4.005 1985 5.94 5.864 5.598 5.211 4.978 4.188 1986 5.356 5.295 5.072 4.902 4.766 4.099 1987 5.862 5.789 5.518 5.063 4.965 4.259 1988 5.704 5.646 5.432 5.19 5.029 4.375 1989 5.37 5.31 5.091 4.859 4.716 4.1 1990 5.281 5.223 5.009 4.766 4.605 3.976 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 5.94 5.864 5.598 5.211 5.029 4.375 0.0645161290322581 5.862 5.789 5.518 5.19 4.978 4.259 0.0967741935483871 5.704 5.646 5.432 5.063 4.965 4.188 0.129032258064516 5.532 5.472 5.253 5.021 4.852 4.145 0.161290322580645 5.491 5.429 5.202 4.913 4.766 4.114 0.193548387096774 5.392 5.331 5.161 4.902 4.74 4.1 0.225806451612903 5.37 5.31 5.103 4.883 4.728 4.099 0.258064516129032 5.356 5.295 5.091 4.879 4.716 4.093 Page 99 of 206 0.290322580645161 5.318 5.264 5.074 4.859 4.711 4.085 0.32258064516129 5.315 5.26 5.072 4.801 4.648 4.034 0.354838709677419 5.307 5.25 5.039 4.797 4.647 4.005 0.387096774193548 5.282 5.223 5.019 4.774 4.619 3.986 0.419354838709677 5.281 5.221 5.009 4.767 4.61 3.984 0.451612903225806 5.228 5.172 4.997 4.766 4.605 3.981 0.483870967741936 5.227 5.169 4.955 4.729 4.58 3.976 0.516129032258065 5.191 5.135 4.93 4.716 4.574 3.963 0.548387096774194 5.166 5.11 4.93 4.706 4.574 3.931 0.580645161290323 5.144 5.09 4.908 4.684 4.541 3.896 0.612903225806452 5.119 5.056 4.893 4.651 4.506 3.881 0.645161290322581 5.085 5.029 4.825 4.607 4.461 3.829 0.67741935483871 5.042 4.985 4.774 4.533 4.384 3.777 0.709677419354839 5.029 4.971 4.757 4.521 4.38 3.733 0.741935483870968 4.806 4.749 4.542 4.298 4.149 3.66 0.774193548387097 4.762 4.703 4.488 4.249 4.105 3.447 0.806451612903226 4.68 4.624 4.42 4.184 4.044 3.406 0.838709677419355 4.537 4.497 4.308 4.06 3.912 3.262 0.870967741935484 4.314 4.26 4.064 3.828 3.687 3.042 0.903225806451613 4.108 4.05 3.839 3.614 3.484 2.654 0.935483870967742 2.936 2.887 2.709 2.491 2.355 1.742 0.967741935483871 1.983 1.936 1.767 1.609 1.505 0.8175 0.1 5.6868 5.6286 5.4141 5.0588 4.9537 4.1837 Average of yearly averages: 3.68215 Inputs generated by pe4. pl  8 August 2003 Data used for this run: Output File: PPZORGsE Metfile: w24232. dvf PRZM scenario: ORgrassseedC. txt EXAMS environment file: pond298. exv Chemical Name: Propiconazole Description Variable Name Value Units Comments Molecular weight mwt 342.23 g/ mol Henry's Law Const. henry atm m^ 3/ mol Vapor Pressure vapr 1.0e 6 torr Solubility sol 110 mg/ L Kd Kd mg/ L Koc Koc 648 mg/ L Photolysis half life kdp 0 days Half life Aerobic Aquatic Metabolism kbacw 138.4 days Halfife Anaerobic Aquatic Metabolism kbacs 0 days Halfife Aerobic Soil Metabolism asm 69.2 days Halfife Hydrolysis: pH 7 0 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.252 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 01 05 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 14 days Set to 0 or delete line for single app. Interval 2 interval 14 days Set to 0 or delete line for single app. Interval 3 interval 14 days Set to 0 or delete line for single app. Record 17: FILTRA Page 100 of 206 IPSCND 1 UPTKF Record 18: PLVKRT PLDKRT 0.0198 FEXTRC 0.5 Flag for Index Res. Run IR Pond Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

stored as PPZGAPnE. out Chemical: Propiconazole PRZM environment: GAPecansC. txt modified Tueday, 22 April 2003 at 07: 57: 20 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 16: 33: 30 Metfile: w93805. dvf modified Wedday, 3 July 2002 at 09: 04: 32 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 2.051 1.997 1.815 1.601 1.505 0.8493 1962 2.902 2.843 2.743 2.524 2.43 1.656 1963 3.812 3.753 3.516 3.355 3.159 2.224 1964 7.302 7.138 6.58 6.122 6.012 3.917 1965 11.59 11.34 10.41 9.155 8.429 5.89 1966 10.03 9.847 9.184 8.644 8.091 6.144 1967 9.457 9.284 8.64 7.729 7.337 5.689 1968 6.531 6.438 6.187 5.803 5.549 4.478 1969 5.016 4.946 4.747 4.538 4.376 3.512 1970 5.582 5.482 5.118 4.812 4.695 3.605 1971 4.84 4.772 4.574 4.381 4.25 3.363 1972 8.954 8.838 8.402 7.98 7.56 4.8 1973 14.2 13.92 13.18 11.97 11.36 7.722 1974 12.21 11.99 11.26 10.23 9.559 7.286 1975 9.911 9.795 9.529 9.179 8.908 6.699 1976 9.564 9.396 8.873 7.935 7.406 5.758 1977 8.212 8.074 7.523 6.854 6.625 5.235 1978 5.949 5.869 5.618 5.438 5.274 4.301 1979 11.43 11.19 10.79 9.435 8.806 5.866 1980 8.32 8.191 7.726 7.089 6.836 5.391 1981 5.619 5.547 5.285 5.053 4.932 4.062 1982 8.717 8.512 7.801 6.783 6.221 4.487 1983 9.043 8.872 8.253 7.897 7.431 5.383 1984 8.851 8.717 8.396 8.065 7.872 5.742 1985 7.977 7.825 7.263 6.496 6.075 4.929 1986 7.177 7.039 6.744 6.1 5.723 4.577 1987 13 12.82 11.77 10.51 9.671 6.207 1988 8.093 7.987 7.768 7.425 7.002 5.53 1989 7.732 7.605 7.295 6.907 6.651 5.013 1990 6.493 6.394 6.187 5.84 5.626 4.386 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 14.2 13.92 13.18 11.97 11.36 7.722 0.0645161290322581 13 12.82 11.77 10.51 9.671 7.286 0.0967741935483871 12.21 11.99 11.26 10.23 9.559 6.699 Page 101 of 206 0.129032258064516 11.59 11.34 10.79 9.435 8.908 6.207 0.161290322580645 11.43 11.19 10.41 9.179 8.806 6.144 0.193548387096774 10.03 9.847 9.529 9.155 8.429 5.89 0.225806451612903 9.911 9.795 9.184 8.644 8.091 5.866 0.258064516129032 9.564 9.396 8.873 8.065 7.872 5.758 0.290322580645161 9.457 9.284 8.64 7.98 7.56 5.742 0.32258064516129 9.043 8.872 8.402 7.935 7.431 5.689 0.354838709677419 8.954 8.838 8.396 7.897 7.406 5.53 0.387096774193548 8.851 8.717 8.253 7.729 7.337 5.391 0.419354838709677 8.717 8.512 7.801 7.425 7.002 5.383 0.451612903225806 8.32 8.191 7.768 7.089 6.836 5.235 0.483870967741936 8.212 8.074 7.726 6.907 6.651 5.013 0.516129032258065 8.093 7.987 7.523 6.854 6.625 4.929 0.548387096774194 7.977 7.825 7.295 6.783 6.221 4.8 0.580645161290323 7.732 7.605 7.263 6.496 6.075 4.577 0.612903225806452 7.302 7.138 6.744 6.122 6.012 4.487 0.645161290322581 7.177 7.039 6.58 6.1 5.723 4.478 0.67741935483871 6.531 6.438 6.187 5.84 5.626 4.386 0.709677419354839 6.493 6.394 6.187 5.803 5.549 4.301 0.741935483870968 5.949 5.869 5.618 5.438 5.274 4.062 0.774193548387097 5.619 5.547 5.285 5.053 4.932 3.917 0.806451612903226 5.582 5.482 5.118 4.812 4.695 3.605 0.838709677419355 5.016 4.946 4.747 4.538 4.376 3.512 0.870967741935484 4.84 4.772 4.574 4.381 4.25 3.363 0.903225806451613 3.812 3.753 3.516 3.355 3.159 2.224 0.935483870967742 2.902 2.843 2.743 2.524 2.43 1.656 0.967741935483871 2.051 1.997 1.815 1.601 1.505 0.8493 0.1 12.148 11.925 11.213 10.1505 9.4939 6.6498 Average of yearly averages: 4.82337666666667 Inputs generated by pe4. pl  8 August 2003 Data used for this run: Output File: PPZGAPnE Metfile: w93805. dvf PRZM scenario: GAPecansC. txt EXAMS environment file: pond298. exv Chemical Name: Propiconazole Description Variable Name Value Units Comments Molecular weight mwt 342.23 g/ mol Henry's Law Const. henry atm m^ 3/ mol Vapor Pressure vapr 1.0e 6 torr Solubility sol 110 mg/ L Kd Kd mg/ L Koc Koc 648 mg/ L Photolysis half life kdp 0 days Half life Aerobic Aquatic Metabolism kbacw 138.4 days Halfife Anaerobic Aquatic Metabolism kbacs 0 days Halfife Aerobic Soil Metabolism asm 69.2 days Halfife Hydrolysis: pH 7 0 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.252 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Page 102 of 206 Application Date Date 01 04 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 14 days Set to 0 or delete line for single app. Interval 2 interval 14 days Set to 0 or delete line for single app. Interval 3 interval 14 days Set to 0 or delete line for single app. Record 17: FILTRA IPSCND 1 UPTKF Record 18: PLVKRT PLDKRT 0.0198 FEXTRC 0.5 Flag for Index Res. Run IR Pond Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

stored as PPZGAPhE. out Chemical: Propiconazole PRZM environment: GAPeachesC. txt modified Satday, 12 October 2002 at 16: 59: 56 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 16: 33: 30 Metfile: w03813. dvf modified Wedday, 3 July 2002 at 09: 04: 32 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.142 1.109 0.9917 0.8388 0.7544 0.367 1962 2.309 2.246 2.022 1.676 1.536 0.9092 1963 2.281 2.234 2.05 1.826 1.697 1.178 1964 2.651 2.595 2.436 2.165 1.992 1.369 1965 2.113 2.073 1.936 1.799 1.702 1.301 1966 2.463 2.432 2.284 2.012 1.856 1.334 1967 2.33 2.286 2.129 1.987 1.874 1.387 1968 3.374 3.304 3.073 2.631 2.401 1.641 1969 2.368 2.329 2.195 1.988 1.857 1.47 1970 2.126 2.087 1.955 1.761 1.638 1.243 1971 2.665 2.606 2.405 2.061 1.889 1.288 1972 2.044 2.008 1.876 1.741 1.648 1.227 1973 3.167 3.097 2.82 2.386 2.199 1.476 1974 2.959 2.897 2.672 2.34 2.173 1.569 1975 2.326 2.284 2.132 1.942 1.82 1.41 1976 4.822 4.704 4.39 3.712 3.347 2.047 1977 2.732 2.69 2.549 2.315 2.171 1.782 1978 2.306 2.267 2.132 1.921 1.794 1.398 1979 2.224 2.182 2.04 1.812 1.682 1.241 1980 1.987 1.95 1.816 1.619 1.494 1.1 1981 3.062 2.981 2.693 2.25 2.064 1.387 1982 2.218 2.18 2.06 1.857 1.73 1.335 1983 2.502 2.449 2.265 2.017 1.904 1.355 1984 3.395 3.32 3.026 2.567 2.368 1.621 1985 2.327 2.287 2.151 1.936 1.808 1.42 1986 2.059 2.02 1.885 1.679 1.549 1.165 1987 1.926 1.887 1.749 1.566 1.451 1.057 1988 1.873 1.837 1.706 1.518 1.416 1.028 1989 2.087 2.044 1.904 1.674 1.543 1.078 1990 1.897 1.86 1.727 1.53 1.409 1.022 Page 103 of 206 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 4.822 4.704 4.39 3.712 3.347 2.047 0.0645161290322581 3.395 3.32 3.073 2.631 2.401 1.782 0.0967741935483871 3.374 3.304 3.026 2.567 2.368 1.641 0.129032258064516 3.167 3.097 2.82 2.386 2.199 1.621 0.161290322580645 3.062 2.981 2.693 2.34 2.173 1.569 0.193548387096774 2.959 2.897 2.672 2.315 2.171 1.476 0.225806451612903 2.732 2.69 2.549 2.25 2.064 1.47 0.258064516129032 2.665 2.606 2.436 2.165 1.992 1.42 0.290322580645161 2.651 2.595 2.405 2.061 1.904 1.41 0.32258064516129 2.502 2.449 2.284 2.017 1.889 1.398 0.354838709677419 2.463 2.432 2.265 2.012 1.874 1.387 0.387096774193548 2.368 2.329 2.195 1.988 1.857 1.387 0.419354838709677 2.33 2.287 2.151 1.987 1.856 1.369 0.451612903225806 2.327 2.286 2.132 1.942 1.82 1.355 0.483870967741936 2.326 2.284 2.132 1.936 1.808 1.335 0.516129032258065 2.309 2.267 2.129 1.921 1.794 1.334 0.548387096774194 2.306 2.246 2.06 1.857 1.73 1.301 0.580645161290323 2.281 2.234 2.05 1.826 1.702 1.288 0.612903225806452 2.224 2.182 2.04 1.812 1.697 1.243 0.645161290322581 2.218 2.18 2.022 1.799 1.682 1.241 0.67741935483871 2.126 2.087 1.955 1.761 1.648 1.227 0.709677419354839 2.113 2.073 1.936 1.741 1.638 1.178 0.741935483870968 2.087 2.044 1.904 1.679 1.549 1.165 0.774193548387097 2.059 2.02 1.885 1.676 1.543 1.1 0.806451612903226 2.044 2.008 1.876 1.674 1.536 1.078 0.838709677419355 1.987 1.95 1.816 1.619 1.494 1.057 0.870967741935484 1.926 1.887 1.749 1.566 1.451 1.028 0.903225806451613 1.897 1.86 1.727 1.53 1.416 1.022 0.935483870967742 1.873 1.837 1.706 1.518 1.409 0.9092 0.967741935483871 1.142 1.109 0.9917 0.8388 0.7544 0.367 0.1 3.3533 3.2833 3.0054 2.5489 2.3511 1.639 Average of yearly averages: 1.30684 Inputs generated by pe4. pl  8 August 2003 Data used for this run: Output File: PPZGAPhE Metfile: w03813. dvf PRZM scenario: GAPeachesC. txt EXAMS environment file: pond298. exv Chemical Name: Propiconazole Description Variable Name Value Units Comments Molecular weight mwt 342.23 g/ mol Henry's Law Const. henry atm m^ 3/ mol Vapor Pressure vapr 1.0e 6 torr Solubility sol 110 mg/ L Kd Kd mg/ L Koc Koc 648 mg/ L Photolysis half life kdp 0 days Half life Aerobic Aquatic Metabolism kbacw 138.4 days Halfife Anaerobic Aquatic Metabolism kbacs 0 days Halfife Aerobic Soil Metabolism asm 69.2 days Halfife Page 104 of 206 Hydrolysis: pH 7 0 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.126 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 01 05 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 5 days Set to 0 or delete line for single app. Interval 2 interval 5 days Set to 0 or delete line for single app. Interval 3 interval 5 days Set to 0 or delete line for single app. Record 17: FILTRA IPSCND 1 UPTKF Record 18: PLVKRT PLDKRT 0.0198 FEXTRC 0.5 Flag for Index Res. Run IR Pond Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

stored as PPZFLScE. out Chemical: Propiconazole PRZM environment: FLsweetcornC. txt modified Satday, 12 October 2002 at 16: 43: 14 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 16: 33: 30 Metfile: w12844. dvf modified Wedday, 3 July 2002 at 09: 04: 30 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 3.491 3.39 3.064 2.467 1.656 0.4083 1962 4.464 4.366 4.023 3.473 2.67 1.869 1963 6.436 5.336 4.928 4.447 3.467 2.61 1964 12.84 12.63 11.67 8.586 6.54 4.591 1965 9.131 9.011 8.57 7.875 7.475 5.673 1966 7.924 7.82 7.558 7.145 6.931 5.336 1967 6.264 6.153 5.756 5.364 5.273 4.284 1968 5.934 5.827 5.569 4.922 4.362 3.672 1969 7.428 7.3 6.89 5.77 5.006 4.147 1970 6.956 6.87 6.584 6.195 6.043 4.676 1971 8.224 8.065 7.62 6.894 5.387 4.015 1972 8.55 8.365 7.918 7.011 5.541 4.508 1973 6.457 6.385 6.166 5.839 5.605 4.371 1974 8.014 7.846 7.396 6.381 5.84 4.653 1975 6.536 6.445 6.136 5.624 5.342 4.242 1976 6.674 6.548 6.255 5.707 4.665 4.034 1977 11.23 11.05 10.38 8.252 6.405 4.743 1978 10.7 10.49 10.03 9.248 7.783 6.316 1979 9.397 9.311 8.937 8.305 7.939 6.137 1980 8.03 7.932 7.452 6.762 6.65 5.313 1981 7.954 7.808 7.378 6.701 5.706 4.706 1982 13.23 12.92 12.34 10.75 8.253 5.831 1983 10.48 10.41 10.06 9.645 9.274 7.074 1984 27.03 26.34 23.89 16.56 12.28 7.396 Page 105 of 206 1985 17.76 17.53 16.69 15.28 14.49 10.42 1986 13.28 13.01 12.11 10.27 9.813 7.758 1987 11.42 11.28 10.76 9.872 9.381 7.27 1988 8.105 8.067 7.905 7.471 7.216 5.605 1989 5.831 5.721 5.504 5.16 4.98 4.042 1990 5.408 5.301 4.942 4.53 4.34 3.442 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 27.03 26.34 23.89 16.56 14.49 10.42 0.0645161290322581 17.76 17.53 16.69 15.28 12.28 7.758 0.0967741935483871 13.28 13.01 12.34 10.75 9.813 7.396 0.129032258064516 13.23 12.92 12.11 10.27 9.381 7.27 0.161290322580645 12.84 12.63 11.67 9.872 9.274 7.074 0.193548387096774 11.42 11.28 10.76 9.645 8.253 6.316 0.225806451612903 11.23 11.05 10.38 9.248 7.939 6.137 0.258064516129032 10.7 10.49 10.06 8.586 7.783 5.831 0.290322580645161 10.48 10.41 10.03 8.305 7.475 5.673 0.32258064516129 9.397 9.311 8.937 8.252 7.216 5.605 0.354838709677419 9.131 9.011 8.57 7.875 6.931 5.336 0.387096774193548 8.55 8.365 7.918 7.471 6.65 5.313 0.419354838709677 8.224 8.067 7.905 7.145 6.54 4.743 0.451612903225806 8.105 8.065 7.62 7.011 6.405 4.706 0.483870967741936 8.03 7.932 7.558 6.894 6.043 4.676 0.516129032258065 8.014 7.846 7.452 6.762 5.84 4.653 0.548387096774194 7.954 7.82 7.396 6.701 5.706 4.591 0.580645161290323 7.924 7.808 7.378 6.381 5.605 4.508 0.612903225806452 7.428 7.3 6.89 6.195 5.541 4.371 0.645161290322581 6.956 6.87 6.584 5.839 5.387 4.284 0.67741935483871 6.674 6.548 6.255 5.77 5.342 4.242 0.709677419354839 6.536 6.445 6.166 5.707 5.273 4.147 0.741935483870968 6.457 6.385 6.136 5.624 5.006 4.042 0.774193548387097 6.436 6.153 5.756 5.364 4.98 4.034 0.806451612903226 6.264 5.827 5.569 5.16 4.665 4.015 0.838709677419355 5.934 5.721 5.504 4.922 4.362 3.672 0.870967741935484 5.831 5.336 4.942 4.53 4.34 3.442 0.903225806451613 5.408 5.301 4.928 4.447 3.467 2.61 0.935483870967742 4.464 4.366 4.023 3.473 2.67 1.869 0.967741935483871 3.491 3.39 3.064 2.467 1.656 0.4083 0.1 13.275 13.001 12.317 10.702 9.7698 7.3834 Average of yearly averages: 4.97141 Inputs generated by pe4. pl  8 August 2003 Data used for this run: Output File: PPZFLScE Metfile: w12844. dvf PRZM scenario: FLsweetcornC. txt EXAMS environment file: pond298. exv Chemical Name: Propiconazole Description Variable Name Value Units Comments Molecular weight mwt 342.23 g/ mol Henry's Law Const. henry atm m^ 3/ mol Vapor Pressure vapr 1.0e 6 torr Solubility sol 110 mg/ L Page 106 of 206 Kd Kd mg/ L Koc Koc 648 mg/ L Photolysis half life kdp 0 days Half life Aerobic Aquatic Metabolism kbacw 138.4 days Halfife Anaerobic Aquatic Metabolism kbacs 0 days Halfife Aerobic Soil Metabolism asm 69.2 days Halfife Hydrolysis: pH 7 0 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.126 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.16 fraction of application rate applied to pond Application Date Date 01 11 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 7 days Set to 0 or delete line for single app. Interval 2 interval 7 days Set to 0 or delete line for single app. Interval 3 interval 7 days Set to 0 or delete line for single app. Record 17: FILTRA IPSCND 1 UPTKF Record 18: PLVKRT PLDKRT 0.0198 FEXTRC 0.5 Flag for Index Res. Run IR Pond Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

stored as PPZORScE. out Chemical: Propiconazole PRZM environment: ORswcornC. txt modified Satday, 12 October 2002 at 17: 21: 42 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 16: 33: 30 Metfile: w24232. dvf modified Wedday, 3 July 2002 at 09: 06: 10 Water segment concentrations ( ppb)