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REACH

Thiophanate-methyl

EC number: 245-740-7 | CAS number: 23564-05-8

Life Cycle description
Uses advised against

Environmental fate & pathways

Biodegradation in water and sediment: simulation tests

Currently viewing:

Administrative data

Link to relevant study record(s)

Reference 1

Endpoint:

biodegradation in water: sediment simulation testing

Type of information:

experimental study

Adequacy of study:

key study

Study period:

1999-07-15 to 2001-05-10

Reliability:

1 (reliable without restriction)

Rationale for reliability incl. deficiencies:

comparable to guideline study

Qualifier:

according to guideline

Guideline:

other: Abbaubarkeit und Verbleib von Pflanzenschutzmitteln im Wasser/Sediment System. Teil IV: 5-1, Dezember 1990. BBA Richtlinien für die Prüfung von Pflanzenschutzmitteln im Zulassungsverfahren.

Version / remarks:

December 1990

Deviations:

Qualifier:

according to guideline

Guideline:

other: SETAC (Europe): Procedures for assessing the environmental fate and ecotoxicity of pesticides

Version / remarks:

March 1995

Deviations:

GLP compliance:

yes (incl. QA statement)

Radiolabelling:

yes

Remarks:

14C-Thiophanate-methyl

Oxygen conditions:

aerobic

Inoculum or test system:

natural water

Details on source and properties of surface water:

Details on source and properties of sediment:

- Details on collection: The water/sediment systems sampled from a river (Rhine river/RheinsuIz AG/Switzerland) and from a pond (Ormalingen BL/Switzerland), consisted of natural water filtered through a 0.2 mm sieve and the uppermost 5 - 10 cm of the sediment sieved through a 2 mm mesh. The water was sampled at a depth of 10 - 30 cm and the sediment was sampled from the top 5 - 10 cm of each system. The sampling sites were located 1 - 2 m from firm land.
- Storage conditions: in sealed containers that were stored at about 4 °C
- Storage length: 3 days until start of acclimation
- River - Textural classification (USDA classification):
Sand (%; > 50 pm): 61.05
Silt (%; 2-50 µm): 27.65
Clay (%; < 2 µm): 11.30
- Pond - Textural classification (USDA classification):
Sand (%; > 50 pm): 38.35
Silt (%; 2-50 µm): 34.50
Clay (%; < 2 µm): 27.15
- River - Textural classification (DIN classification):
Sand (%; > 50 pm): 54.30
Silt (%; 2-50 µm): 34.40
Clay (%; < 2 µm): 11.30
- Pond - Textural classification (DIN classification):
Sand (%; > 50 pm): 32.20
Silt (%; 2-50 µm): 40.65
Clay (%; < 2 µm): 27.15
- pH at time of collection: 7.61 – 7.83
- Organic carbon (g C/100 g dry sediment: 0.97 (river sediment); 6.13 (pond sediment)
- Redox potential (mv):
Initial: -36 mV (river sediment); -79 mV (pond sediment)
Final: -90 mV (river sediment); -170/-128 mV (pond sediment)
- Biomass: 42550 – 274000 (river sediment); 21500 – 6000 (Pond sediment)
- Sediment samples sieved: yes

Duration of test (contact time):

>= 100 - <= 301 d

Initial conc.:

0.2 mg/L

Based on:

test mat.

Parameter followed for biodegradation estimation:

CO2 evolution

radiochem. meas.

Details on study design:

TEST CONDITIONS
- Volume of test solution/treatment: 4.23 mg test item/ 10 mL acetonitrile
- Test temperature: 20 ± 1 °C

TEST SYSTEM
- Culturing apparatus: gas-flow-system in 1000 mL glass metabolism flasks (inner diameter: about 10.6 cm, area: about 88.2 cm2
- Test performed in closed vessels due to significant volatility of test substance: yes
- Test performed in open system: no
- Details of trap for CO2 and volatile organics if used: Samples were connected to a series of two traps, the first trap contained 50 mL ethylene glycol and the second trap 50 mL 2N NaOH in order to trap volatile compounds.

SAMPLING
- Sampling frequency: After 0, 1, 2, 8, 16, 30, 58 and 100 days of incubation one sample of each system was taken for analysis. Additional samples were taken for the pond system after 140, 202 and 301 days of incubation.

STATISTICAL METHODS: Degradation rates were determined in the study. Calculations were performed with a commercially available computer program (Excel 97) using up to fifteen decimal places. These results are now superseded by the kinetic re-evaluation performed in accordance with FOCUS (2006, 2014) (Kiesel and Geibel, 2015i and j).

Compartment:

natural water / sediment

% Recovery:

100.1

St. dev.:

4.5

Remarks on result:

other: River water/sediment system

Compartment:

natural water / sediment

% Recovery:

97.3

St. dev.:

4.7

Remarks on result:

other: Pond water/sediment system

Compartment:

natural water: freshwater

DT50:

1.6 d

Type:

other: Single First Order (SFO)

Temp.:

20 °C

Remarks on result:

other: River water

Compartment:

natural water: freshwater

DT50:

2.8 d

Type:

other: Single First Order (SFO)

Temp.:

20 °C

Remarks on result:

other: pond water

Key result

Compartment:

natural water / sediment: freshwater

DT50:

3.5 d

Type:

other: Single First Order (SFO)

Temp.:

20 °C

Remarks on result:

other: Pond water / sediment system

Key result

Compartment:

natural water / sediment: freshwater

DT50:

1.6 d

Type:

other: Single First Order (SFO)

Temp.:

20 °C

Remarks on result:

other: River / sediment system

Transformation products:

yes

No.:

Details on transformation products:

Please refer to the attached tables for the details representation of the formation and decline of each major and minor metabolite for each label and test dose.

Evaporation of parent compound:

yes

Volatile metabolites:

Residues:

Details on results:

TEST CONDITIONS
- Aerobicity, moisture, temperature and other experimental conditions maintained throughout the study: Yes
- Anomalies or problems encountered: none

MAJOR TRANSFORMATION PRODUCTS
- Range of maximum concentrations in % of the applied amount and day(s) of incubation when observed:
Carbendazim/MBC, max 81.6 % (8 days), 35.3 % (100 days)
4-OH-TM, max 9.5 % (8 day), 3.1 % (58 days),
Additionally metabolites AV-1951 and 2-AB were detected reaching maximum amounts of 6.3 % (day 2) and 6.5 % (day 16) of the applied radioactivity, respectively.

MINOR TRANSFORMATION PRODUCTS
- Range of maximum concentrations in % of the applied amount at end of study period:
Beside the known metabolites up to 7 minor unknown degradation products (i.e. not corresponding to retention times of available reference items) were detected, none of them exceeded a maximum individual level of 3.2 % of the radioactivity applied.

EXTRACTABILITY OF RADIOACTIVITY FROM SEDIMENT
The total radioactivity extracted from the river sediment increased to a maximum of 60.4 % of the applied radioactivity on day 58 and decreased to 41.3 % at the end of incubation (day 100). Soxhlet extractions recovered a maximum of 25.8 % of the applied radioactivity (day 100).
The total radioactivity extracted from the pond sediment increased to a maximum of 63.5 % of the applied radioactivity on day 58 and subsequently decreased to 43.6 % and 17.6 % of the applied radioactivity on days 100 and 301, respectively. Soxhlet extractions recovered a maximum of 16.3 % of the applied radioactivity (day 202).
Additionally, harsh extractions using acetonitrile/2N hydrochloric acid (8:2) under reflux performed on the sediment samples of the 100-day interval recovered 5.4 % (river) and 3.5 % (pond) of the applied radioactivity. Harsh extractions performed for the sediment of the 301-day interval of the pond system recovered 5.7 % of the applied radioactivity.

NON- EXTRACTABILITY OF RADIOACTIVITY FROM SEDIMENT
The non-extractable radioactivity increased with time up to 48.1 % and 40.6 % of the applied radioactivity after 100 days of incubation for the river and pond systems, respectively. At the end of incubation of the pond system (301 days) the non-extractable radioactivity amounted to 70.0 % of the applied radioactivity.

MINERALISATION
Mineralization of the parent item was low amounting to 1.3 % and 1.6 % of applied radioactivity after 100 days of incubation for the river and pond systems, respectively. In the pond system the amount of 14carbondioxide increased to 5.2 % on day 301 of incubation.

Degradation rates were determined in the study. These results are now superseded by the kinetic re-evaluation performed in accordance with FOCUS (2006, 2014) (Kiesel and Geibel, 2015i and j).

During incubation, the oxygen content in water samples varied from 4.2 to 8.3 mg/L in the pond system and from 4.5 to 8.2 mg/L in the river system. The redox potential in water ranged from 115 to 210 mV in the pond system and from 140 to 203 mV in the river system. In the sediment the redox potential varied between – 77 and -161 mV in the pond system and between -108 and -205 mV in the river system, confirming reductive conditions. The pH in the pond system varied between 7.67 and 8.38 and between 7.86 and 8.42 in the river system.

The material balance for the pond and river test systems after treatment with ¹⁴C-thiophanate-methyl is given in the tables below:

Table 1: Mass balance for River water / sediment system. As % of applied radioactivity, single replicates.

Fraction	Incubation time (d)
Fraction	0	1	2	8	16	30	58	100
Water	105.9	87.0	80.0	43.4	30.9	20.1	10.2	3.3
Sediment	1.2	15.8	25.3	55.9	65.7	77.1	87.5	89.4
¹⁴CO₂	-	< 0.1	< 0.1	< 0.1	0.1	0.2	0.7	1.3
volatiles	-	< 0.1	< 0.1	< 0.1	< 0.1	< 0.1	< 0.1	< 0.1
Total	107.1	102.8	105.2	99.3	96.7	97.5	98.5	94.0

Table 2: Mass balance for Pond water/sediment system. As % of applied radioactivity, single replicates.

Fraction	Incubation time (d)
Fraction	0	1	2	8	16	30	58	100
Water	101.6	94.9	86.9	51.1	42.5	32.0	10.1	5.5
Sediment	0.8	6.8	14.6	49.0	58.5	66.7	84.1	84.2
¹⁴CO₂	-	< 0.1	< 0.1	0.2	0.4	0.9	1.0	1.6
volatiles	-	< 0.1	< 0.1	< 0.1	< 0.1	< 0.1	< 0.1	< 0.1
Total	102.5	101.6	101.5	100.3	101.4	99.6	95.3	91.3

Table 3: Characterisation of radioactivity in Pond water/sediment system. As % of applied radioactivity.

Fraction

Sample

Incubation time (d)

100

140*

202*

301*

Parent

Water

Sedim.

Total

98.4

85.9

2.0

87.8

66.5

6.0

72.5

9.7

8.1

17.9

6.1

0.9

7.4

8.3

- -

MBC

Water

Sedim.

Total

2.7

6.5

2.4

8.9

14.8

5.5

20.3

34.3

28.4

67.2

38.2

36.9

75.1

26.8

36.7

63.5

8.0

46.5

54.5

2.6

30.2

32.8

1.7

18.3

20.0

1.9

18.7

20.5

0.4

4.7

5.1

4-OH-TM

Water

Sedim.

Total

0.2

2.8

2.3

5.1

2.3

5.0

7.3

2.9

5.7

8.6

4.6

1.4

1.5

0.6

0.5

AV-1951

Water

Sedim.

Total

0.5

2.6

0.4

2.9

5.6

0.6

6.1

2.3

1.5

3.8

1.8

2-AB

Water

Sedim.

Total

2.3

0.5

7.0

7.5

6.0

6.2

3.9

0.3

2.9

3.2

M10

Water

Sedim.

Total

2.1

2.4

4.5

0.9

2.9

3.8

1.4

5.3

6.7

2.2

6.1

8.3

1.7

7.7

9.3

0.8

7.7

8.5

1.0

6.1

7.1

¹⁴CO₂

non extractable

0.2

< 0.1

2.0

< 0.1

1.9

0.2

5.1

0.4

6.2

0.9

8.9

1.0

20.7

1.6

40.6

4.7

48.5

2.5

52.1

5.2

70.0

Total

101.8

101.6

101.5

100.3

101.4

99.6

95.3

91.3

92.1

90.9

95.2

* Data from these sampling days were not presented in Addendum 7 to the Monograph of 13 November 1997 (2003).

Table 4: Characterisation of radioactivity in River water/sediment system. As % of applied radioactivity.

Fraction

Sample

Incubation time (d)

100

Parent

Water

Sedim.

Total

103.2

69.2

48.4

0.4

MBC

Water

Sedim.

Total

2.8

14.4

9.0

23.5

25.3

16.7

42.0

39.0

42.6

81.6

27.3

42.8

70.1

17.3

48.7

66.1

9.4

50.4

59.8

2.3

33.0

35.3

4-OH-TM

Water

Sedim.

Total

0.6

1.4

4.4

5.1

9.5

1.3

4.7

6.0

1.4

3.8

5.2

3.1

AV-1951

Water

Sedim.

Total

3.4

6.3

2-AB

Water

Sedim.

Total

0.7

5.8

6.5

4.8

4.7

4.8

M10

Unknown

Water

Sedim.

Total

1.6

1.3

0.8

2.2

3.1

0.7

2.4

3.2

¹⁴CO₂

non extractable

0.4

< 0.1

5.5

< 0.1

6.3

< 0.1

7.3

0.1

11.3

0.2

19.9

0.7

27.1

1.3

48.1

Total

106.3

102.8

105.2

99.3

96.7

97.5

98.5

94.0

Table 5: Kinetic parameters and the resulting DT50/90 values for thiophanate-methyl and its metabolites carbendazim (MBC), 4-OH-TM, 2-AB and M10 for the total water/sediment systems. Results for thiophanate-methyl are from parent only fits, other results are from pathway fits. From kinetic evaluation in Kiesel and Geibel (2015i, j) based on data in Völkl (2001).

Substance	System	kinetic model	Mo	χ², % error		parameter	Confidence interval		Prob. > t	DT₅₀ (days)	DT₉₀ (days)
							lower	upper
Thiophanate-methyl	Pond	SFO	105.18		6.7	k = 0.199	0.16	0.24	10 x 10^-5	3.5	11.6
MBC		SFO-SFO	0		8.5	k = 9.09 x 10^-3	7.4 x 10^-3	0.011	9.8 x 10^-13	76.2	253.2
4-0H-TM		SFO-SFO	0		33	k = 1.22 x 10^-3	5.2 x 10 ³	0.019	0.0008	56.7	188.4
2-AB		SFO-SFO	0		22	k = 1.27 x 10^-3	5.1 x 10^-3	0.020	0.001	54.7	181.8
M10 *		SFO-SFO	0		12	k = 1.45 x 10^-3	-7.0 x 10^-4	0.004	0.10	478.5 ^a	>1000
Thiophanate-methyl	River	SFO	108.39		3.3	k = 0.424	0.38	0.47	2.1 x 10^-4	1.6	5.4
MBC		SFO-SFO	0	6.4		k = 7.6 x 10^-3	0.0051	0.010	1.2 x 10^-5	91.6	304.2
4-OH-TM		SFO-SFO	0	38		k = 0.0182	-1.3 x 10^-3	0.038	0.043	38.2 ^a	126.8

* The results for M10 are from separate pathway fit parent → dummy → M10.

^a Results not considered acceptable by the RMS.

NOTE:

^a Graphs of results not considered statistically reliable or acceptable by member states (RMS) were not shown and this does not affect the validity of the study or the kinetic evaluation of the results. This is because the initial results of this study are now superseded by the kinetic re-evaluation performed in accordance with FOCUS (2006, 2014) (Kiesel and Geibel, 2015i and j). During peer review the applicant was requested to submit degradation rates for the water/sediment systems for metabolites 4-OH-TM and 2-AB considering only the data from maximum occurrence onwards. These data were provided in Moshenberg and Drechsler (2017a, b). The results presented above are all from the revised kinetic re-evaluation. Thus, the study is valid and reliable.

Validity criteria fulfilled:

yes

Conclusions:

Degradation rates were determined in this study. The degradation kinetics of the test item was re-evaluated by Kiesel and Geibel (2015i, j) based on the data from this study by Völkl (2001). The assessment was conducted according to the FOCUS degradation kinetics guidance (2006, 2014) using the model KinGUI 2.1. Thus, the results from this study are now superseded by the kinetic re-evaluation.
In the river system, the DT50 value obtained for 14C-labelled test item was 1.6 days for the disappearance from the water phase and the total system. The corresponding DT90 value was 5.4 days.
In the pond system, the DT50 value obtained for 14C-labelled test item were 3.5 days for the dissipation from the water phase and the total system. The corresponding DT90 value was 11.6 days.
The mineralization of the test item, i.e. the formation of 14CO2, accounted for a maximum of 1.3 % and 1.6 %/5.2 % of the applied radioactivity for the river (day 100) and pond systems (day 100/301), respectively. Other volatile compounds did not exceed 0.1 % of the applied radioactivity.

Executive summary:

In the present study, the route and rate of degradation of ¹⁴C-test item, was investigated in two equilibrated water/sediment systems on the basis of the SETAC Guideline "Procedure for assessing the environmental fate and ecotoxicity of pesticides (March 1995, Part 8, 8.2) and the BBA Guideline, "Abbaubarkeit und Verbleib von Pflanzenschutzmitteln im Wasser/Sediment System" (Teil IV: 5-1, Dezember 1990) to satisfy the data requirements of the European Community Commission Directive 95/36/EC of July 14, 1995; paragraph 7.2.1.3.2 Water/Sediment Study amending Council Directive 91/414/EEC Annex I, 7.2.1.

The water/sediment systems sampled from a river (Rhine river/RheinsuIz AG/Switzerland) and from a pond (Ormalingen BL/Switzerland), consisted of natural water filtered through a 0.2 mm sieve and the uppermost 5-10 cm of the sediment sieved through a 2 mm mesh.

The test systems were equilibrated at 20 ± 1 °C, in the dark for about 3 weeks before treatment. By this time, pH values, redox potential and oxygen concentration in water had reached constant values. Thereafter, the radiolabeled test item was applied to the water surface using a micro-syringe at a target concentration of 0.2 mg/L in order to be able to follow the degradation of the test item. This concentration corresponds to an application rate of 600 g test item/ha, assuming a uniform substance distribution within a 30 cm water layer. During the entire incubation period, the aquatic systems were aerated, but the sediments remained undisturbed. Air leaving the test systems was passed sequentially through ethylene glycol and sodium hydroxide to trap organic volatiles and CO₂, respectively.

Samples were taken for analysis at day 0, 1, 2, 8, 16, 30, 58 and 100 for both systems. Additional samples were taken for the pond system after 140, 202 and 301 days of incubation. After sampling, the radioactivity in water and extractable radioactivity from sediment was separately measured by LSC and analysed by HPLC and TLC. A total radioactivity balance and the distribution of radioactivity in each sample were established at each sampling interval.

Total mean recoveries obtained during the incubation period were 100.1 % ± 4.5 % and 97.3 % ± 4.7 % of the applied radioactivity for the river and pond system, respectively.

The radioactivity present in the water phases of both test systems decreased continuously throughout the incubation period, reaching levels of 43.4 % (river) and 51.1 % (pond) after 8 days of incubation, and decreasing further to 3.3 % (river) and 5.5 % (pond) of applied radioactivity on day 100. The radioactivity in the pond water decreased to 2.4 % after 301 days of incubation. Concurrently, extractable radioactivity from sediments increased continuously reaching maximum amounts of 60.4 % for river and 63.5 % for pond on day 58. Thereafter, the extractable radioactivity decreased to values of 41.3 % (day 100; river) and 43.6 % and 17.6 % (day 100 and day 301; pond).

The amount of non-extractable radioactivity steadily increased during incubation. On day 100, 48.1 % and 40.6 % of the applied radioactivity remained unextracted from the river and pond sediments, respectively. Thereafter, it increased to 70.0 % on day 301 for the pond system. Additional harsh extraction using acetonitrile/2N hydrochloric acid (8:2; v/v) carried out for the day 100 (river and pond) and day 301 (only pond) samples, extracted 5.4 % (river) and 3.5 %/ 5.7 % (pond, day 100/301) of the applied radioactivity. After all extractions, sediment samples of day 100 and day 301 (only pond) were also submitted to organic matter fractionation. About 36 % and 33 %/ 54 % (day 100/301) of the applied radioactivity in the river and pond sediment, respectively, was bound to the immobile organic fractions of the sediment, i.e. the humic acid and the humin fractions. The radioactivity associated with the fulvic acids fraction amounted to about 6 % and 4 %/ 11 % (day 100/ 301) of the applied radioactivity for the river and pond sediments, respectively.

The mineralization of the test item, i.e. the formation of ¹⁴CO₂, accounted for a maximum of 1.3 % and 1.6 %/5.2 % of the applied radioactivity for the river (day 100) and pond systems (day 100/301), respectively. Other volatile compounds did not exceed 0.1 % of the applied radioactivity.

After treatment, the amount of test item decreased continuously in both pond and river whole systems. At the start of incubation (day 0), the parent item represented 103.2 % (river) and 98.4 % (pond) of the applied radioactivity. The test item was present in the river and pond system until days 8 and 30 amounting to 0.4 % and 8.3 % of the applied radioactivity, respectively.

In the river system, the parent item was degraded to at least 11 components. Four components were characterised as 4-OH-TM (M2), AV-1951 (M3), Carbendazim/MBC (M5), and 2-AB (M9) based on their chromatographic behaviour using high performance liquid chromatography in comparison with authentic reference items.

Carbendazim/MBC (M5) was detected as the main degradation product. Carbendazim/MBC was detected from day 0 onwards reaching a maximum of 81.6% on day 8 and decreasing thereafter to 35.3 % on day 100.

The degradation products 4-OH-TM (M2), AV-1951 (M3) and 2-AB (M9) reached maximum amounts of 9.5 % (day 8), 6.3 (day 2) and 6.5 % (day 16) of the applied radioactivity, respectively.

Additionally, up to 7 minor unknown degradation products were detected, not exceeding 5 % of the applied radioactivity.

In the pond system, the parent item was degraded to at least 19 components, Carbendazim/MBC (M5) being the main degradation product. Carbendazim/MBC was detected from day 0 onwards and increased to a maximum of 75.1 % of applied radioactivity on day 16. At the end of incubation (day 301) it amounted to 5.1 %.

Degradation products 4-OH-TM (M2), AV-1951 (M3), 2-Aminobenzimidazole (M9) and radioactive fraction M10 were detected at maximum amounts of 8.6 % (day 30), 6.1 % (day 2), 7.5 % (day 58) and 9.3 % (day 140), respectively. Additionally, several minor unknown degradation products were detected, not exceeding 5 % of the applied radioactivity.

Mineralization played a minor role while the degradation and incorporation of metabolites to the organic matter of the sediment can be regarded as an important way of disappearance of the test item and its degradates from both aquatic systems.

The results show that ¹⁴C-labelled test item was degraded by partial hydrolysis of one side chain to metabolite AV-1951, and following formation of the benzimidazole ring, to its main metabolite Carbendazim. Carbendazim was further hydrolysed to 2-aminobenzimidazole (2-AB) however, the major part of radioactivity was incorporated into the organic matter of the sediment.

In the river system, the DT₅₀value obtained for ¹⁴C-labelled test item was 1.6 days for the disappearance from the water phase and the total system. The corresponding DT₉₀ value was 5.4 days.

In the pond system, the DT₅₀ value obtained for ¹⁴C-labelled test item were 3.5 days for the dissipation from the water phase and the total system. The corresponding DT₉₀ value was 11.6 days.

Reference 2

Endpoint:

biodegradation in water: simulation testing on ultimate degradation in surface water

Type of information:

experimental study

Adequacy of study:

key study

Study period:

2014-01-09 to 2014-10-14

Reliability:

1 (reliable without restriction)

Rationale for reliability incl. deficiencies:

guideline study

Qualifier:

according to guideline

Guideline:

OECD Guideline 309 (Aerobic Mineralisation in Surface Water - Simulation Biodegradation Test)

Version / remarks:

2004

Deviations:

GLP compliance:

yes (incl. QA statement)

Radiolabelling:

yes

Remarks:

[Ring-U-14C] -Thiophanate-methyl

Oxygen conditions:

aerobic

Inoculum or test system:

natural water: freshwater

Details on source and properties of surface water:

- Details on collection: Fountains Abbey, Ripon, UK
- Storage conditions: the water was stored in the dark in an environmental chamber routinely maintained at 4 ± 2 °C, with free access to air.
- Temperature (°C) at time of collection: 6.4 - 8.3 °C
- pH at time of collection: 7.92 – 8.73
- Oxygen concentration (mg/L) initial/final: 6.1 to 9.4 mg/L

Duration of test (contact time):

30 d

Initial conc.:

0.095 mg/L

Based on:

other: [14C]-thiophanate-methyl (radioactivity) high test concentration

Initial conc.:

0.01 mg/L

Based on:

other: [14C]-thiophanate-methyl (radioactivity) low test concentration

Parameter followed for biodegradation estimation:

radiochem. meas.

Details on study design:

TEST CONDITIONS
- Volume of test solution/treatment: 100 mL natural water
- Sterile conditions: Samples of pelagic water were sterilised twice by autoclaving (121 °C, 2.2 bar, 30 minutes). Glass units, unit heads, tubing and PTFE magnetic stirring bars were similarly sterilised.
- Additional substrate: no
- Solubilising agent: acetone
- Test temperature: 6.4 °C
- pH: 7.6 to 9.0
- pH adjusted: yes
- Aeration of dilution water: yes, inlet and outlet air was passed through a bacterial air filter to maintain sterility
- Continuous darkness: yes
- Any indication of the test material adsorbing to the walls of the test apparatus: yes

TEST SYSTEM
Route and rate of degradation of thiophanate-methyl was studied in natural water from a lake (pelagic system) at a high (95 µg/L) and a low concentration (10 µg/L). The test system consisted of glass flasks, connected to two 2M NaOH, traps to capture CO2. Each flask was aerated with moistened air.
Air passing through sterilised samples was passed through bacterial air filters positioned at the inlet and outlet of each flask to maintain sterility.
Samples (100 mL) of natural water (100 µm sieved) were used in the tests. The water used had a suspended solids concentration of 2.94 mg/L. Thiophanate-methyl dissolved in acetone was applied onto the water surface using a syringe.

SAMPLING
- Sampling Intervals: Duplicate units were removed for analysis from non-sterile groups treated with the test item at 0, 1, 2, 4, 7, 14 and 30 day after treatment (DAT). Duplicate sterilised samples were removed from sterilised incubation groups at 0 and 2 DAT.

DESCRIPTION OF CONTROL AND/OR BLANK TREATMENT PREPARATION
CONTROL AND BLANK SYSTEM
- Number of culture flasks/concentration: 2 flask for the Solvent reference control and two flasks for the blank each.

STATISTICAL METHODS:
Degradation rates were determined in the study by kinetic evaluation in accordance with FOCUS (2006, 2014) and using KingUI 2.1 Software. The results presented below are all from the revised kinetic re-evaluation.

Reference substance:

benzoic acid, sodium salt

Compartment:

natural water: freshwater

% Recovery:

98.7

Remarks on result:

other:

Remarks:

High concentration 0.01 mg/L (0 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

96.9

Remarks on result:

other:

Remarks:

High concentration 0.01 mg/L (2 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

98.3

Remarks on result:

other:

Remarks:

Low concentration 0.01 mg/L (30 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

95.1

Remarks on result:

other:

Remarks:

High concentration 0.095 mg/L (0 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

98.1

Remarks on result:

other:

Remarks:

High concentration 0.095 mg/L (2 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

95.1

Remarks on result:

other:

Remarks:

High concentration 0.095 mg/L (30 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

98.9

Remarks on result:

other:

Remarks:

High concentration 0.095 mg/L – sterile (0 DAT); Aqueous phase + organic unit wash

Compartment:

natural water: freshwater

% Recovery:

100

Remarks on result:

other:

Remarks:

Originally reported value: 100.2 % High concentration – sterile (2 DAT); Aqueous phase + organic unit wash

% Degr.:

99.3

Parameter:

radiochem. meas.

Sampling time:

2 d

Remarks on result:

other: High concentration - sterile (95 µg/L) (levels of thiophanate-methyl and metabolites measured in the natural water from each incubation group)

Key result

% Degr.:

93.2

Parameter:

radiochem. meas.

Sampling time:

30 d

Remarks on result:

other: High dose 95 µg/L (levels of thiophanate-methyl and metabolites measured in the natural water from each incubation group)

Key result

% Degr.:

96.4

Parameter:

radiochem. meas.

Sampling time:

30 d

Remarks on result:

other: Low concentration 10 µg/L (levels of thiophanate-methyl and metabolites measured in the natural water from each incubation group)

Key result

Compartment:

natural water / sediment: freshwater

DT50:

2.2 d

Type:

other: Single First-Order (SFO)

Temp.:

20 °C

Remarks on result:

other: High dose at 95 µg/L

Key result

Compartment:

natural water / sediment: freshwater

DT50:

0.64 d

Type:

other: Double First-Order in Parallel (DFOP)

Temp.:

20 °C

Remarks on result:

other: Low dose at 10 µg/L

Compartment:

natural water / sediment: freshwater

DT50:

1.5 d

Type:

other: Single First order (SFO)

Temp.:

20 °C

Remarks on result:

other: Low dose at 10 µg/L (represents best fit)

Compartment:

natural water: freshwater

DT50:

1.3 d

Type:

other: First order Multi Component (FOMC)

Temp.:

20 °C

Remarks on result:

other: Low dose at 10 µg/L

Compartment:

natural water: freshwater

DT50:

2.3 d

Type:

other: Single first order (SFO)

Temp.:

20 °C

Remarks on result:

other: High dose at 95 µg/L (represents best fit)

Compartment:

natural water: freshwater

DT50:

2.3 d

Type:

other: First order Multi Component (FOMC)

Temp.:

20 °C

Remarks on result:

other: High dose at 95 µg/L

Other kinetic parameters:

other: Double First Order in Parallel (DFOP)

Transformation products:

yes

No.:

Details on transformation products:

Please refer to the attached tables for the details representation of the formation and decline of each major and minor metabolite for each label and test dose.

Evaporation of parent compound:

Volatile metabolites:

Residues:

not specified

Details on results:

Results with reference substance:

Radiochemical Purity

The radiochemical purity of the stock solution of [¹⁴C]-thiophanate-methyl was determined by HPLC and found to be > 97 %. The radiochemical purity of thiophanate-methyl within AS3 was determined by HPLC before treatment and was found to be 95.7 %.

Treatment Rate

The definitive application rate for the low concentration rate (90 µL of AS4) was 1.016 µg/unit. The definitive application rate for the high concentration rate and sterile units (96 µL of AS3) was 9.776 µg/unit. This is equivalent to 10.16 and 97.76 µg/L respectively, based on a water volume of 100 mL. The coefficients of variation for the concentration checks were < 3 %, thus the application solutions can be assumed to be homogenous.

Test System Parameters

Fountains Abbey water used in the definitive test had a temperature of 6.4 °C and a pH of 8.73 at the time of collection. Measurements of pH and oxygen concentrations in control vessels at each sampling interval showed pH values in the range 7.6 to 9.0 and oxygen concentrations in the range 6.1 to 9.4 mg/L. The oxygen levels show that the water was aerobic. There was no difference in the values obtained between the two replicates (i.e. addition and no addition of acetone).

Mass Balance

The sterile sample was selected for analysis at 2 DAT as the screening test showed > 89 % degradation by 7 DAT. It was estimated that the DT-50 of thiophanate-methyl would be ca. 3 days, thus in order to obtain meaningful data and chromatography from the sterile sample, the unit was sampled at 2 DAT.

Distribution did not change significantly over the 30 day incubation period. Results from the two application rates and the sterilised sample were similar, with the vast majority of applied radioactivity associated with the water (> 93 % AR).

Thiophanate-methyl did not appreciably mineralise in any group (maximum of 0.5 % AR observed as volatiles). Little radioactivity was recovered in the organic wash of the unit (maximum of 1.5 % AR), therefore it can be assumed that there was no adsorption to the glass vessels. The organic wash samples were not analysed chromatographically as they all contained < 2 % AR.

Time (DAT)	Incubation group	Treatment rate (µg/L)	Recovery of radioactivity (% AR)
Time (DAT)	Incubation group	Treatment rate (µg/L)	Aqueous	Organic wash	Traps	Mass balance
0	A (10 µg/L)	10	97.7	1.0	NA	98.7
30	A (10 µg/L)	10	96.4	1.4	0.5	98.3
0	B (95 µg/L)	95	94.2	1.0	NA	95.1
30	B (95 µg/L)	95	93.2	1.5	0.5	95.1
0	C (Sterile)	95	98.3	0.6	NA	98.9
2	C (Sterile)	95	99.3	0.9	ND	100.2

NA = Not applicable, ND = Not detected or < 0.1 % AR

Metabolism of Thiophanate-methyl in Natural Water

Following application of test item to non-sterile samples, levels of total thiophanate-methyl rapidly decreased, such that by 14 DAT none remained. MBC was the dominant metabolite with occurrences of up to 73 and 83 % AR for the high and low test concentration, respectively. Further metabolites FH-432, 2-AB as well as the two unknown metabolites (UM1 and UM2) were considered major metabolites. DX-105 and CM-0237 were detected as minor metabolites at single occasions. The potential transformation products 4-OH-TM, AV-1951 and CM-0238 were not detected within this study. Other metabolites were detected, but at levels of < 5 % AR, thus they were not further characterised. The table below summarises the levels of major metabolites' (as % AR) at 0 DAT, 30 DAT and their maxima.

Test item concentration (µg/L)	Moiety	Recovery of radioactivity (% AR)
Test item concentration (µg/L)	Moiety	0 DAT	30 DAT	Maximum
10	Thiophanate- methyl	61.1*	ND	61.1 (0)
95	Thiophanate- methyl	89.1*	ND	89.1 (0)
10	MBC	31.3	59.3	82.8 (14)
95	MBC	2.3	72.0	73.4(14)
10	FH-432	2.9	ND	5.6 (1)
95	FH-432	ND	ND	11.3 (4)
10	2-AB	ND	9.5	9.5 (30)
95	2-AB	ND	6.4	6.4 (30)
10	UM1	0.7	11.4	11.4 (30)
95	UM1	ND	8.7	8.7 (30)
10	UM2	ND	8.0	8.0 (30)
95	UM2	ND	5.3	5.3 (30)

*Thiophanate-methyl rapidly degraded to MBC (up to 31.3 % AR) at 0 DAT in units treated at a concentration of 10 µg/L. By comparison, in units treated at a concentration of 95 µg/L, MBC accounted for 2.3 % AR at 0 DAT. Values in parentheses indicate the sampling interval (DAT) at which the maxima was reached.

The sterile units showed a similar profile, with thiophanate-methyl degrading rapidly to MBC and FH-432 (via DX-105). The table below summarises the data obtained from the sterile units.

Time (DAT)

	Incubation group	Treatment rate (µg/L)	Recovery of radioactivity (% AR)
	Incubation group	Treatment rate (µg/L)	Thiophanate-methyl	MBC	FH-432	Total*
0	C (Sterile)	95	92.1	4.2	ND	98.3
2	C (Sterile)		67.1	23.4	6.9	99.3

Comparison of the levels of MBC formed at 2 DAT in the sterile units (23 % AR) and non-sterile units (39 - 60 % AR) suggested that its production, thus thiophanate-methyl degradation, was part chemical (hydrolysis) and part microbial.

Rate of Degradation of Thiophanate-methyl in Natural Water

SFO kinetics provided a good fit to the data for the 95 µg/L application rate (group B), although slightly better fits were obtained using FOMC kinetics for the samples treated with the 10 µg/L application rate (group A). Including other statistical parameters, e.g. the confidence interval, which includes zero for some fits, SFO fits are considered appropriate also for the low test concentrations.

A step-wise assessment of the degradation kinetics was conducted in accordance with FOCUS degradation kinetics guidance (Geibel & Lobe, 2016, and Geibel & Moshenberg, 2016). For the low dose test system thiophanate-methyl and degradation products carbendazim (MBC) and UM1 were considered; for the high dose test system thiophanate-methyl, carbendazim (MBC) and FH-432. FH-432 was not considered for the low dose system and UM1 not for the high dose system due to too few data points. Conceptually, all three metabolites were treated as primary metabolites. 2-AB and UM2 could not be included in the analyses as they were only detected occasionally. Data from both replicates were used and time zero amounts of metabolites were added to the parent compartment. The results are presented in tables and figures below (graphs not shown for statistically not reliable results).

Table 1: Kinetic evaluation for thiophanate-methyl; lake water treated at low (10 µg/L) dose. Results for thiophanate-methyl are from parent only fit. From Geibel & Lobe (2016) and Geibel & Moshenberg (2016) based on data from Hurst (2015).

Substance	Dose rate	kinetic model	Mo	χ², % error	parameter	Lower Confidence interval	prob > t	DT50 (days)	DT90 (days)
Thiophanate-methyl	Low	SFO	94.29	14.0	k = 0.8096	0.66	5.4 x 10^-7	0.86	2.8
		FOMC	95.95	3.0	α = 1.223	0.87	n.r.	0.63	4.6
		FOMC	95.95	3.0	ß = 0.829	0.42	n.r.	0.63	4.6
		DFOP	95.99	2.1	k1 = 1.7342	1.1	4.2 x 10-4	0.64	5.0
					k2 = 0.2332	0.13	1.4 x 10^-3
					g = 0.6763	0.53	8.4 x 10^-6
		HS	96.00	2.7	k1 = 0.9836	0.89	1.1 x 10^-8	0.70	5.0
					k2 = 0.2663	0.18	1.5 x 10^-4
					tb = 1.34	1.0	7.3 x 10^-6
MBC	Low	DFOP-SFO	n.r.	6.4	k = 0.01070	0.0034	0.0035	64.8	215
UM1	Low	DFOP-SFO	n.r.	15.8	k = 2.33 x 10^-14	-0.017	0.50	>1000	>1000

n.r. Not relevant

Both application rates gave similar DT₅₀values for thiophanate-methyl (ca. 1 - 2 days) and similar DT₉₀ values (ca. 5 - 8 days) measured by SFO kinetics.

DT₅₀ values were overestimated and DT₉₀ values were underestimated, although were not dissimilar to values obtained from the FOMC kinetic model due to the rapid degradation.

Table 2: Kinetic evaluation for thiophanate-methyl; lake water treated at high (95 μg/L) dose. Results for thiophanate-methyl are from parent only fit. From Geibel & Lobe (2016) and Geibel & Moshenberg (2016) based on data from Hurst (2015).

Substance	Dose rate	kinetic model	Mo	χ², % error	parameter	Lower Confidence interval	prob > t	DT50 (days)	DT90 (days)
Thiophanate-methyl	High	SFO	91.66	2.5	k = 0.3142	0.28	1.0 x 10^-8	2.2	7.3
		FOMC	92.28	2.4	α = 10.65	-26.6 -86.5	n.r.	- ^a	- ^a
		FOMC	92.28	2.4	ß = 31.86	-26.6 -86.5	n.r.	- ^a	- ^a
MBC	High	SFO-SFO	n.r.	1.2	k = 6.419 x 10^-4	-0.0038	0.39	>1000	>1000
FH-432	High	SFO-SFO	n.r.	7.1	k = 0.1334	0.10	3.6 x 10^-11	5.2	17.3

n.r. Not relevant

a Not considered acceptable.

At the low concentration (10 μg/L) FOMC provided a lower Chi² error-% than SFO and additional biphasic models were therefore used. DFOP was selected as the best fit model for thiophanate-methyl. At the high test concentration (95 µg/L), the SFO model provided a good fit to the data for the parent whereas FOMC parameters were not reliable.

For the metabolites acceptable results were obtained for carbendazim (MBC) in the low dose system and for FH-432 (high dose system). The authors apparently accepted also the results for UM1 (low dose) and carbendazim (MBC) (high dose) but since the rate constants did not pass the t-test the RMS did not consider these results reliable.

Table 3: Formation fractions of carbendazim (MBC), FH-432 and UM1, according to kinetic re-analyses by Geibel & Lobe (2016) and Geibel & Moshenberg (2016) of the data of from Hurst (2015).

Degradation pathway	Dose rate	Formation fraction	Standard deviation
Thiophanate-methyl → MBC	Low	0.901	0.045
Thiophanate-methyl → MBC	High	0.768 ^a	0.044
Thiophanate-methyl → UM1	Low	0.099 ^a	0.070
Thiophanate-methyl → FH-432	High	0.232	0.074

^a Result not considered reliable by the RMS since the corresponding rate constant was not reliable (p-values > 0.10).

NOTE:

^a Graphs of results not considered statistically reliable or acceptable by member states (RMS) were not shown and this does not affect the validity of the study or or the kinetic evaluation of the results results. This is because the initial results of the study are superseded by kinetic re-evaluations performed in accordance with FOCUS (2006, 2014) and using KinGUI 2.1 software. Although, the first kinetic re-evaluation (Giebel & Lobe, 2015, and Geibel, 2015) was not accepted by the RMS since erroneous input data were used for the optimisations and since the KinGUI results were not presented in Word or pdf format. During the evaluation the applicant therefore submitted a revised kinetic re-evaluation (Giebel & Lobe, 2015, and Geibel & Moshenberg, 2016). The results presented above are all from the revised kinetic re-evaluation. Thus, the study is valid and reliable.

Confirmation of Transformation Products by TLC

TLC analysis of selected samples showed qualitative comparison to results obtained by HPLC. Quantitatively the results were different on occasion; although this was attributed to degradation of the samples during storage as TLC analysis was performed up to 3 months after sample collection.

Proposed Metabolic Pathway

Thiophanate-methyl degraded into the transient primary metabolite DX-105 (seen only at 0 and 1 DAT), by oxidation of thiourea to urea. Further degradation to FH-432 (observed from 0 DAT) occurred by oxidation of the second thiourea to urea, and to CM-0237 (observed in a single sample at 7 DAT) by cyclisation to form an imidazole ring.

Thiophanate-methyl also degraded significantly immediately after application, to the principal metabolite MBC via the loss of a carbonothioyl side chain and cyclisation to form an imidazole ring. The unidentified metabolite (referred to as UM1), also measured at 0 DAT, was formed by a loss of methylurea from the molecule followed by the cyclization of the molecule to form a thiotriazone ring. By 14 DAT, MBC had begun to degrade to 2-AB following loss of methylurea, whilst UM1 began to degrade to UM2 by oxidation of thiourea to urea at 30 DAT.

Degradation of [¹⁴C]-Sodium Benzoate

There was little difference in the degradation of [¹⁴C]-sodium benzoate to ¹⁴CO₂ when acetone was added or withheld from the test units. Degradation of 84.7 % (no acetone added) or 93.1 % (addition of acetone) show that the water contained a viable population of microorganisms capable of mineralising sodium benzoate thereby validating the system for use with thiophanate-methyl.

Repeatability and sensitivity of analytical method

Each of the samples analysed in duplicate showed a difference to each other of up to 30 %, which amounted to difference in AR of up to < 6 %, therefore the analytical method can be considered to be reproducible.

Limit of detection

The limit of detection (LOD) for chromatographic analysis by HPLC and TLC were estimated based on the smallest metabolites that were detected once background radioactivity had been deducted. The results showed values of 1.3 % AR for 10 µg/L samples and 1.4 % AR for 95 µg/L samples by HPLC and values of 0.4 and 0.9 % AR in the 10 µg/L samples and 95 µg/L samples by TLC, respectively. The limit of quantification (LOQ) was assumed to equal the LOD.

Validity criteria fulfilled:

yes

Conclusions:

The results from this study were re-evaluated by Geibel & Lobe (2016) and Geibel & Moshenberg (2016) in a step-wise assessment of the degradation kinetics in accordance with FOCUS degradation kinetics guidance by single first order (SFO), first order multi-component (FMOC) and Double first order in parallel (DFOP) methods. The DT50 was determined to be 0.64 days (low dose) and 2.2 day (high dose).

Executive summary:

The aerobic biodegradation of [¹⁴C]-thiophanate-methyl has been studied in the laboratory at two concentrations (10 and 95 µg/L) in natural surface water according to OECD 309 under pelagic conditions. Individual samples were incubated under dark conditions at 20 ± 2 °C for up to 30 days after treatment (DAT). Samples (100 mL) of the natural water (100 µm sieved) were used in the tests. The water used had a suspended solids concentration of 2.94 mg/L. The natural water pH during the test was between 7.6 and 9.0 and the water was maintained under aerobic conditions (oxygen concentrations 6.1 to 9.4 mg/L) under the experimental conditions employed.

Comparison of the reference unit treated with acetone and that not treated with acetone showed similar results. In both units, > 80 % of the applied benzoate had mineralised within 14 days, showing that the water was microbially active with or without the addition of acetone. Comparison of the blank control unit treated with acetone and that not treated with acetone showed similar water quality results.

There was almost no mineralisation (≤ 0.5 % AR) and most of the radioactivity remained in the natural water. Minimal amounts of AR were detected in the organic vessel wash. Total recovery of radioactivity (mass balance) was > 95 % AR in all units.

The conditions of the test were suitable for studying aerobic mineralisation in water judged by the extensive mineralisation of a control reference substance, [¹⁴C]-sodium benzoate within two weeks.

Under these conditions, the test item degraded extensively producing the principal transformation product MBC. Two other metabolites, namely FH-432 and UM1 were formed at >10 % AR. By the end of the 30 day study, two other transformation products were considered as major metabolites; 2-AB (up to 9.5 % AR) along with UM2 (up to 8 % AR).

Degradation was attributable to chemical and biological processes.

Minor transformation products CM-0237 and DX-105 were observed during the course of the study at levels of < 5 % AR.

The test item and its transformation products did not appreciably mineralise within the 30 day study.

The test item degraded quickly in non-sterilised units, with a degradation rate DT-50 values of < 3 days at application rates of 10 and 95 µg/L. Degradation in sterile units was observed, but to a lesser extent as 67 % test item was measured at 2 DAT. The DT50 was determined to be 0.64 days (low dose) and 2.2 day (high dose).

Description of key information

Biodegradation in water and sediment: simulation tests-Surface water

The results from this study was re-evaluated by Geibel & Lobe (2016) and Geibel & Moshenberg (2016) in a step-wise assessment of the degradation kinetics in accordance with FOCUS degradation kinetics guidance by single first order (SFO), first order multi-component (FMOC) and Double first order in parallel (DFOP) methods. The DT₅₀ was determined to be 0.64 days (low dose) and 2.2 day (high dose).

Biodegradation in water and sediment: simulation tests-sediment

In the river system, the DT₅₀ value obtained for ¹⁴C-labelled test item was 1.6 days for the disappearance from the water phase and the total system. The corresponding DT90 value was 5.4 days.

In the pond system, the DT₅₀ value obtained for ¹⁴C-labelled test item were 3.5 days for the dissipation from the water phase and the total system. The corresponding DT90 value was 11.6 days.

Key value for chemical safety assessment

Half-life in freshwater:: 0.64 d
at the temperature of:: 20 °C

Additional information

Simulation tests-surface water:

There was almost no mineralisation (≤ 0.5 % AR (Recovery of radioactivity))

) and most of the radioactivity remained in the natural water. Minimal amounts of AR were detected in the organic vessel wash. Total recovery of radioactivity (mass balance) was > 95 % AR in all units.

Degradation was attributable to chemical and biological processes.

Minor transformation products CM-0237 and DX-105 were observed during the course of the study at levels of < 5 % AR.

The test item and its transformation products did not appreciably mineralise within the 30 day study.

Simulation tests-sediment:

Total mean recoveries obtained during the incubation period were 100.1 % ± 4.5 % and 97.3 % ± 4.7 % of the applied radioactivity for the river and pond system, respectively.

The amount of non-extractable radioactivity steadily increased during incubation. On day 100, 48.1 % and 40.6 % of the applied radioactivity remained unextracted from the river and pond sediments, respectively. Thereafter, it increased to 70.0 % on day 301 for the pond system. Additional harsh extraction using acetonitrile/2N hydrochloric acid (8:2; v/v) carried out for the day 100 (river and pond) and day 301 (only Pond) samples, extracted 5.4 % (river) and 3.5 %/ 5.7 % (pond, day 100/301) of the applied radioactivity. After all extractions, sediment samples of day 100 and day 301 (only Pond) were also submitted to organic matter fractionation. About 36 % and 33 %/ 54 % (day 100/301) of the applied radioactivity in the river and pond sediment, respectively, was bound to the immobile organic fractions of the sediment, i.e. the humic acid and the humin fractions. The radioactivity associated with the fulvic acids fraction amounted to about 6 % and 4 %/ 11 % (day 100/ 301) of the applied radioactivity for the river and pond sediments, respectively.

Carbendazim/MBC (M5) was detected as the main degradation product. Carbendazim/MBC was detected from day 0 onwards reaching a maximum of 81.6% on day 8 and decreasing thereafter to 35.3 % on day 100.

The degradation products 4-OH-TM (M2), AV-1951 (M3) and 2-AB (M9) reached maximum amounts of 9.5 % (day 8), 6.3 (day 2) and 6.5 % (day 16) of the applied radioactivity, respectively.

Additionally, up to 7 minor unknown degradation products were detected, not exceeding 5 % of the applied radioactivity.

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Thiophanate-methyl

Biodegradation in water and sediment: simulation tests

Administrative data

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Description of key information

Key value for chemical safety assessment

Additional information

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