United States

Environmental Protection Agency Prevention, Pesticides

And Toxic Substances (7101) EPA 712-C-08-018

EPA 712-C-08-019

October 2008 

# Fate, Transport and
Transformation Test
Guidelines

OPPTS 835.4300 Aerobic Aquatic
Metabolism

OPPTS 835.4400 Anaerobic Aquatic
MetabolismINTRODUCTION

This guideline is one of a series of test guidelines that have been developed by the Office of Preventi on, Pesticides and Toxic Substances (OPPTS), United States Environmental Pr otection Agency for use in the testing of pesticides and toxic substances, and the development of test data to meet the data requirements of the A gency under the Toxic Substances Control Act (TSCA) (15 U.S.C. 2601), t he Federal Insecticide, Fu ngicide and Rodenticide Act (FIFRA) (7 U.S.C. 136, et seq. ), and section 408 of t he Federal Food, Drug and Cosmetic (FFDCA) (21 U.S.C. 346a).

OPPTS developed this guideline th rough a process of harmonization of the testing guidance and requirements that existed for the Office of Pollution Prevention and Toxics (OPPT) in Title 40, Chapter I, Subchapter R of the Code of Federal Regulations (C FR), the Office of Pest icide Programs (OPP) in publications of the Nationa l Technical Information Service (NTIS) and in the guidelines published by the Organiza tion for Economic Cooperation and Development (OECD).

For additional information about OPPTS harmonized guidelines and to access this and other guidelines, please go to http://www.epa.gov/oppts and
select “Test Methods & Gui delines” on the left side menu.1 OPPTS 835.4300 Aerobic aquatic metabolism OPPTS 835.4400 Anaerobic aquatic metabolism

. (a) Scope—(1) Applicability. This guideline is intended for use in meeting testing requirements of the Federal Insecticide, Fungi cide, and Rodenticide Act (FIFRA) (7 U.S.C.136, et

seq .) and for testing pursuant to the Toxic S ubstances Control Act (TSCA) (15 U.S.C. 2601, et seq. ) It describes procedures that, if followed, would result in data that would generally be of scientific merit for the purposes described in paragraph (b) of this guideline.

(2) Background . The source materials used in devel oping this OPPTS test guideline are OPP 162-3 Anaerobic aquatic metabolism studies and OPP 162-4 Aerobic aquatic metabolism studies (Pesticide Assessment Guidelines Subdivision N - Chemistry: Environmental Fate, EPA report 540/9- 82-021, October 1982); and OECD Guideline for the Testing of Chemicals 308 Aerobic and Anaerobic Transformation in Aquatic Sediment Systems (OECD, adopted April 2002).

(b) Purpose. (1) Chemicals can enter shallow or deep surface waters by such routes as direct application, spray drift, run-off, drainage, waste di sposal, industrial, domestic or agricultural effluent and atmospheric deposition. The conditions in natura l aquatic sediment systems are often aerobic in the upper water phase. The surface layer of sediment can be either aerobic or anaerobic, whereas the deeper sediment is usually anaerobic. This gui deline describes a laboratory test method to assess aerobic and anaerobic transformation of organic chemi cals in aquatic sediment systems. An aerobic test simulates an aerobic water column over an aerobic sediment layer that is underlain with an anaerobic gradient. An anaerobic te st simulates a completely anaerobic water-sediment system. Such studies are used for chemicals which are directly applied to water or which are likely to reach the aqueous environment by the routes described above.

(2) If circumstances indicate that it is n ecessary to deviate significantly from these recommendations, for example by using intact sedime nt cores or sediments that may have been exposed to the test substance, ot her methods are available for this purpose (see paragraph (h)(1) of this guideline).

(c) Definitions

.

Aerobic transformation (oxidising) reactions are reactions occurring in the presence of molecular oxygen (see paragraph (h)(2) of this guideline).

Anaerobic transformation (reducing) reactions are reactions occurring under exclusion of molecular oxygen (see paragraph (h)(2) of this guideline).

Bound residues represent compounds in soil, plant or anim al that persist in the matrix in the form of the parent substance or its metabolite(s) after extractions. The extraction method should not substantially change the compounds themselves or th e structure of the matrix. The nature of the bond can be clarified in part by matrix-altering extraction methods and sophisticated analytical techniques. To date, for example, covalent ionic and sorptive bonds, as well as entrapments, have been identified in this way. In general, the formation of bound residues reduces the bioaccessibility and the2 bioavailability significantly (see paragraph (h)(3) of this guideline) (modifi ed from IUPAC 1984 (see paragraph (h)(4) of this guideline).

DT 50 (Disappearance Time 50) is the time within which the in itial concentration of the test substance is reduced by 50%.

DT 75 (Disappearance Time 75) is the time within which the initial concentration of the test substance is reduced by 75%.

DT 90 (Disappearance Time 90) is the time within which the initial concentration of the test substance is reduced by 90%.

Half-life, t 0.5 , is the time taken for 50% transforma tion of a test substance when the transformation can be described by first-order kinetic s; it is independent of the initial concentration.

Mineralization is the complete degradation of an organic compound to CO 2 , H 2 O under aerobic conditions, and CH 4 , CO 2 and H 2 O under anaerobic conditions. In the context of this guideline, when radiolabeled compound is used, mineralization mean s extensive degradation of a molecule during which a labeled carbon atom is oxidized or reduced quantitatively with release of the appropriate

amount of 14 CO 2 or 14 CH 4 , respectively.

Natural waters are surface waters obtained from ponds, rivers, streams, etc.

Sediment is a mixture of mineral and organic ch emical constituents, the latter containing compounds of high carbon and nitrogen content and of high molecular masses. It is deposited by

natural water and forms an interface with that water.

Test substance is any substance, whether the parent or relevant transformation products.

Transformation products are all substances resulting from biotic and abiotic transformation reactions of the test substance including CO 2 and bound residues.

(d) General considerations— (1) Principle of the test— (i) Method. The method described in this guideline employs an aerobic and an anaerobi c aquatic sediment system which allows: the

measurement of the transformation rate of the test substance in a water-sediment system; the

measurement of the transformation rate of the test substance in the sediment; the measurement of the

mineralization rate of the test substan ce and/or its transformation products (when 14 C-labeled test substance is used); the identification and quantif ication of transformation products in water and sediment phases including mass balance (when labeled te st substance is used); and the measurement of

the distribution of the test substance and its tr ansformation products between the two phases during a period of incubation in the dark (to avoid, for exam ple, algal blooms) at constant temperature. Existing guidelines are cited at (h)(5) through (h)(9) in this guideline.3 (ii) Half-lives determinations. Half-lives, DT 50 , DT 75 and DT 90 values are determined where the data warrant, but should not be extra polated far past the experimental period.

(iii) Number of sediments . At least two sediments and their associated waters are used for both the aerobic and the anaerobic studies respectivel y (see paragraph (h)(10) of this guideline). However, there may be cases where more than two aquatic sediments should be used, for example, for a chemical that may be present in freshwater and/or marine environments . Sediments should be representative of intended use sites.

(iv) Aerobic test system . The aerobic test system described in this test guideline consists of an aerobic water layer (typical oxygen concentrations ra nge from 7 to 10 mg/L) and a sediment layer,

aerobic at the surface and anaerobic below th e surface (typical average redox potentials (E h ) in the anaerobic zone of the sediment range from –80 to –190 mV). Moistened air is passed over the surface of the water in each incubation unit to maintain sufficient oxygen in the head space.

(v) Anaerobic test system . For the anaerobic test system, the test procedure is essentially the same as that outlined for the aerobic system with the exception that moistened nitrogen is passed

above the surface of the water in each incubation unit to maintain a head space of nitrogen. The sediment and water are regarded as anaerobic once the redox potential (E h ) is lower than –100 mV. In the anaerobic test, assessment of mineralization in cludes measurement of evolved carbon dioxide and

methane.

(vi) Conditions. The conditions in natural aquatic se diment systems are often aerobic in the upper water phase. The surface layer of sediment can be either aerobic or anaerobic, whereas the deeper sediment is usually anaerobic. The aerobic test simulates an aerobic water column over an aerobic sediment layer that is underlain with an anaerobic gradient. The anaerobic test simulates a completely anaerobic water-sediment system. If circumstances indicate that it is necessary to deviate significantly from these recommendations, for example by using intact sediment cores or sediments that may have been exposed to the test substance, other methods are available for this purpose (h)(1).

(vii) Optional preliminary test . If duration and sampling regi me cannot be estimated from other relevant studies on the test substance, an optional preliminary test may be considered appropriate, which should be performed using the same test conditions proposed for the definitive study. Relevant experiment al conditions and results from the preliminary test, if performed, should be briefly reported.

(2) Applicability of the test (i) The method is generally applicable to chemical substances (unlabeled or labeled) for which an analytical method with sufficient accuracy and sensitivity is available. It is applicable to slightly vol atile, non-volatile, water-soluble or poorly water-soluble compounds. The test should not be applied to ch emicals which are highly volatile from water (e.g. fumigants, organic solvents) and thus cannot be kept in water and/or sedime nt under the experimental

conditions of this test.4 (ii) The method has been applied so far to study the transformation of chemicals in fresh waters and sediments, but in principle can also be applied to estuarine/marine systems. It is not suitable to simulate conditions in flowing water (e.g., rivers) or the open sea.

(e) Test procedure —(1) Test substance (i) Non-labeled or isotope -labeled test substance can

be used to measure the rate of transformation alt hough labeled material is pref erred. Labeled material is used for studying the pathwa y of transformation and for establishing a mass balance. 14 C-labeling is recommended, but the use of other isotopes, such as 13 C, 15 N, 3 H, 32 P, may also be useful. As far as possible, the label should be positioned in the most st able part(s) of the molecule. For example, if the substance contains one ring, this ring should be labeled; if the test substance contains two or more rings, separate studies may be needed to evaluate the fate of each labeled ring and to obtain suitable information on formation of transformational products . The chemical and/or radiochemical purity of

the test substance should be at least 95%.

(ii) Before carrying out a test, the following in formation about the test substance should be available: solubility in wa ter; solubility in organic solvents; vapor pressure and Henry’s Law constant; n-octanol/water partition coefficient; adsorption coefficient (K d , K f or K
oc , where appropriate); hydrolysis; dissociation constant (pK

a ); and chemical structure of the test substance and position of the isotope-label(s), if applicable. The temperature at which these measurements were made should be reported.

(iii) Other useful information may include da ta on toxicity of the test substance to microorganisms, data on ready and/or inherent biodegradability, and data on aerobic and anaerobic

transformation in soil.

(2) Analytical methods (i) Analytical methods (including extraction and clean-up methods) for identification and quantification of the test s ubstance and its transformation products in water and

in sediment should be available.

(ii) Reference substances should be used for the identification and quantification of transformation products by spectroscopic and chromatographic methods.

(iii) Recovery. Extraction and analysis of, at least, duplicate water and sediment samples immediately after the addition of the test substance give a first indication of the repeatability of the analytical method and of the uniformity of the applica tion procedure for the test substance. Recoveries for later stages of the experiments are given by the respective mass balances (w hen labeled material is used). Recoveries should range from 90% to 110% for labeled chemicals (see paragraph (h)(9) of this guideline) and from 70% to 110% for non-labeled chemicals.

(iv) Repeatability and sensitivity of analytical method. (A) Repeatability of the analytical method (excluding the initial extraction efficiency) to quantify test substance and transformation products can be checked by dup licate analysis of the same extract of the water or the sediment samples which were incubated long enough for formation of transformation products.5 (B) The limit of detection (LOD) of the analytical method for the test substance and for the transformation products should be at least 0.01 mg·kg -1 in water or sediment (as test substance) or 1% of the initial amount applied to a test system whic hever is lower. The lim it of quantification (LOQ) should also be specified.

(v) Accuracy of transformation data. Regression analysis of the concentrations of the test substance as a function of time gives the appropriate information on the accuracy of the transformation

curve and allows the calculation of the confidence lim its for half-lives (if pseudo first-order kinetics apply) or DT 50 values and, if appropriate, DT 75 and DT 90 values.

(3) Test system and apparatus (i) The study should be perfor med in glass containers (e.g., bottles, centrifuge tubes), unless pre liminary information (such as n-octanol-water partition coefficient, sorption data, etc.) indicates that the test substance may adhere to glass, in which case an alternative material (such as Teflon) may have to be considere d. Where the test substance is known to adhere to glass, it may be possible to alleviate this probl em using one or more of the following methods:

determine the mass of test substance and transforma tion products sorbed to glass; ensure a solvent wash of all glassware at the end of the test; use of formulated products (see also paragraph (f)(3)(iii) of this guideline); and/or use an increased amount of co-solvent for addition of test substance to the system; if a co-solvent is used it should be a co-solvent that does not solvolyze the test substance.

(ii) Examples of typical test apparatus, i.e ., gas flow-through and biom eter-type systems, are shown in Figures 1 and 2, respectively (see also paragraph (h)(11) of this guideline). Other useful incubation systems are described in paragraph (h )(12) of this guideline. The design of the experimental apparatus should permit the exchange of air or nitrogen and the trapping of volatile products. The dimensions of the apparatus should be such that the requirements of the test are complied with (see paragraph (f)(1)). Ventilation may be provided by either gentle bubbling or by passing air or nitrogen over the water surface. In the latter case gentle stirring of the water from above may be advisable for better distribution of the oxygen or nitrogen in the water. CO 2 -free air should not be used as this can result in increases in the pH of the water. In either case, disturbance of the sediment is undesirable and should be avoided as far as possible. Slightly volatile chemicals should be tested in a biometer-type system with gentle sti rring of the water surface. Closed vessels with a headspace of either atmospheric air or nitrogen and internal vials for the trapping of volatile products can also be used (see paragraph (h)(13)of this guide line). Regular exchange of the headspace gas is important in the aerobic test in order to compensate for the oxygen consumption by the biomass.6 Figure 1—Example of a Gas Flow-through Apparatus.

Safety trap, empty

Trap 1: Ethyleneglycol to trap organic volatiles

Trap 2: Sulphuric acid 0.1 M to trap alkaline volatiles.7 Figure 2—Example of a Biometer Apparatus:

(iii) Suitable traps for collecting volatile transf ormation products include but are not restricted

to 1 mol·dm -3 solutions of potassium hydroxide or sodi um hydroxide for carbon dioxide and ethylene glycol, ethanolamine or 2% paraffin in xylene fo r organic compounds. As these alkaline absorption

solutions also absorb the carbon dioxide from the ventilation air and that formed by respiration in aerobic experiments, they have to be exchanged at regular intervals to avoid their saturation and thus loss of their absorption capacity. Volatiles formed unde r anaerobic conditions, such as methane, can be collected, for example, by molecular sieves. Such volatiles can be combusted, for example, to CO 2 by passing the gas through a quartz tube filled with CuO at a temperature of 900 ° C and trapping the CO 2 formed in an absorber with alkali (see paragraph(h)(14) of this guideline).

(iv) Laboratory instrumentation for chemical an alysis of test substance and transformation products is used (e.g., gas liquid chromatography (GLC), high performance liquid chromatography8 (HPLC), thin-layer chromatography (TLC), mass spectroscopy (MS), gas chromatography-mass spectroscopy (GC-MS), liquid chromatography-ma ss spectrometry (LC-MS), nuclear magnetic resonance (NMR), etc.), including detection system s for radiolabeled or non-labeled chemicals as appropriate. When radiolabeled material is use d, a liquid scintillation counter and combustion oxidiser (for the combustion of sediment samples prior to analysis of radioactivity) should be used.

(4) Sediments. Selection and number of aquatic sediments —(i) Sampling sites. The sampling sites should be selected in accordance with th e purpose of the test in any given situation. In selecting sampling sites, the history of possible agricultural, industrial or domestic inputs to the catchment and the waters upstream should be consider ed. Sediments should not be used if they have

been contaminated with the test substance or its st ructural analogues within the previous 4 years. The types of sediments selected should be representativ e of areas where the pesticide will be used or released into the aquatic environment.

(ii) Sediment selection. (A) Two sediments are normally used for the aerobic studies (see paragraph (h)(10) of this guideline. The two sedime nts selected should differ with respect to organic

carbon content and texture. One sediment should have a high organic carbon content (2.5-7.5%) and a fine texture, the other sediment should have a low organic carbon content (0.5-2.5%) and a coarse texture. The difference between the organic carbon contents should normally be at least 2%. "Fine texture" is defined as a (clay + silt) content of >50% and "coarse texture" is defined as a (clay + silt) content of <50%. (Clay + silt) is the mineral fracti on of the sediment with particle size of < 50 μm. The difference in (clay + silt) content for the two se diments should normally be at least 20%. In cases, where a chemical may also reach marine waters, at least one of the water-sediment systems should be of marine origin.

(B) For the strictly anaerobic study, two sediments (including their associated waters) should be sampled from the anaerobic zones of surface wate r bodies (see paragraph (h)(10)of this guideline). Both the sediment and the water phases should be ha ndled and transported caref ully under exclusion of

oxygen.

(C) Other parameters may be important in the sel ection of sediments and should be considered on a case-by-case basis. For example, the pH range of sediments would be important for testing chemicals for which transformation and/or sorp tion may be pH-dependent. pH-dependency of sorption might be reflected by the pK

a of the test substance.

(iii) Characterization of water-sediment samples. (A) Key parameters that should be measured and reported (with reference to the met hod used) for both water and sediment, and the stage of the test at which those parameters are to be de termined are summarised in Table 1. For information, methods for determination of these parameters are gi ven in paragraphs (h)(15) through (h)(20) of this guideline.9 Table 1. Measurement of parameters for characterization of water-sediment samples*

Parameter Stage of Test Procedure

Field Sampling PostHandling Start of

Acclimation Start of Test During Test End of Test

Water Origin/source x Temperature x pH x x x x x TOC x x x O 2 concentration** x x x x x Redox potential** x x x x Sediment Origin/source x Depth of layer x pH x x x x x Particle Size

distribution x

TOC x x x x Microbial biomass*** x x x Redox potential** Observation (color/smell) x x x x

* See paragraphs (h)(10), (h)(21) and (h)(22).

** Recent research results have shown that measurements of water oxygen concentrations and of redox potentials have neither a mechanistic nor a predictive value as far as growth and development of microbial populations in surface water are concerned (see paragraphs (h)(23) and (h)(24) of this guide line). Determination of the biochemical oxygen demand (BOD, at field sampling, start and end of test) and of concentrations of micro/macro nutrients Ca, Mg and Mn (at start and end of test) in water and the measurement of total N and total P in se diments (at field sampling and end of test) may be better tools to interpret and evaluate aerobic biotransformation rates and routes.

*** Microbial respiration rate method (see paragraph (h)(25) of this guideline), fumigation method (see paragraph (h)(26) of this guideline) or plate count measurements (e.g., bacter ia, actinomycetes, fungi and total colonies) for aerobic studies; methanogenesis rate for anaerobic studies.

(B) In addition, other parameters may have to be measured and reported on a case by case basis, e.g., for freshwater: particles, alkalinity, hardness, conductivity, NO 3 /PO 4 (ratio and individual values); for sediments: cation exchange capacity, water holding capacity, carbonate, total nitrogen and phosphorus; and for marine systems: salinity). Analysis of sediments and water for nitrate, sulfate, bioavailable iron, and possibly other electron accep tors may be also useful in assessing redox conditions, especially in relation to anaerobic transformation.

(5) Collection . The draft ISO guidance on sampling of bottom sediment (see paragraph (h)(27) of this guideline) should be used for sampling of sediment. Sediment samples should be taken from the entire 5 to 10 cm upper layer of the sediment. A ssociated water should be collected from the same

site or location and at the same time as the sedime nt. For the anaerobic study, sediment and associated water should be sampled and transported under excl usion of oxygen (see paragraph (h)(28) of this guideline) (see also paragraph (e)(4)(i)(B). Some sa mpling devices are described in the literature (see paragraphs (h)(22), (h)(27) of this guideline).

(6) Handling . The sediment is separated from the water by filtration and the sediment wet-10 sieved to a 2 mm-sieve using excess location water that is then discarded. Then known amounts of

sediments and water are mixed at the desired ratio (see paragraph (f)(2)(i)) in incubation flasks and prepared for the acclimation period (see paragraph (f)(1)). For the anaerobic study, all handling steps have to be done under exclusion of oxygen (see paragr aphs (h)(29) through (h)(33) of this guideline).

(7) Storage . Use of freshly sampled sediment a nd water is strongly recommended, but if storage is necessary, sediment and water should be sieved as described above and stored together, water-logged (6-10 cm water laye r), in the dark, at 4 ± 2 o C for a maximum of 4 weeks (see paragraphs (h)(10), (h)(22), (h)(27) of this guide line). Recent studies have shown that storage at 4 oC can lead to a decrease of the organic carbon content of the sedime nt which may possibly result in a decrease of microbial activity (see paragraph (h)(34) of this gui deline). Samples to be used for aerobic studies should be stored with free access of air (e.g. in ope n containers), whereas those for anaerobic studies under exclusion of oxygen. Freezing of sediment and water and drying- out of the sediment should not occur during transportation and storage.

(f) Test conduct— (1) Preparation of the sediment/water samples for the test . A period of acclimation should take place prior to adding the test substance, with each sediment/water sample being placed in the incubation vessel to be used in the main test, and the acclimation to be carried out under exactly the same conditions as the test inc ubation (see paragraphs (f)(2)(i), (f)(2)(ii)). The acclimation period is the time needed to reach reas onable stability of the system, as reflected by pH, oxygen concentration in water, redox potential of the sediment and water, and macroscopic separation of phases. The period of acclimation should norma lly last between one week and two weeks and should not exceed four weeks. In the aerobic test, the sediment should have a surface layer that is

aerobic at the time of treatment. Results of determinations performed during this period should be reported.

(2) Test conditions . (i) The test should be performed in the incubation apparatus (see paragraphs (e)(3)(i) through (e)(3)( iii)) with a water:sediment volume ratio between 3:1 and 4:1, and a sediment layer of 2.5 cm (± 0.5 cm). A minimum am ount of 50 g of sediment (dry weight basis) per

incubation vessel is recommended.

(ii) The test should be performed in the dark at a constant temperature in the range of 10 to

30 o C. A temperature of (20 ± 2) o C is appropriate. Where appropriate, an additional lower temperature (e.g., 10 ° C) may be considered on a case-by-cas e basis, depending on the information called for from the test. Incubation temperature should be monitored and reported.

(3) Treatment and application of test substance . (i) One test concentration of chemical is

used. Test with a second concentration can be us eful for chemicals that reach surface waters by different entry routes resulting in significantly different concentrations, as long as the lower concentration can be analyzed with sufficient accuracy. For crop protection ch emicals applied directly to water bodies, the maximum dosage on the label s hould be taken as the maximum application rate

calculated on the basis of the surface area of the wate r in the test vessel. For chemicals applied on land, the study should be conducted at the aqueous c oncentration expected when the maximum label rate is applied to a 1-hectare pond, 2-meters deep. In all other cases, the concentration to be used11 should be based on predictions from environmental emi ssions. Care should be taken to ensure that an adequate concentration of test substance is applied in order to characterise the route of transformation and the formation and decline of transformation produc ts. It may be necessary to apply higher doses (e.g.,10 times) in situations where test substance concen trations are close to limits of detection at the start of the study and/or where major transformati on products could not readily be detected when present at 10% of the test substance application rate . However, if higher test concentrations are used they should not have a significant adverse effect on the microbial activity of the water-sediment system. Data from exaggerated dose studies should only be used for degradat e identification purposes.

In order to achieve a constant concentration of test substance in vessels of differing dimensions an adjustment to the quantity of the material applied may be considered appropriate, based on the depth of the water column in the vessel in relation to the dept h of water in the field (w hich is assumed to be 100 cm, but other depths can be used). See the following example calculation.

Example Calculation for Application Dose to Test.

Cylinder internal diameter: =8 cm

Water column depth not including sediment: =12 cm

Surface area: 3.142 x 4 2 =50.3 cm 2

Application rate: 500 g test substance/ha corresponds to 5 μg/cm 2

Total μg: 5 x 50.3 = 251.5 μg

Adjust quantity in relation to a depth of 100 cm:

12 x 251.5 ÷ 100 = 30.18 μg

Volume of water column: 50.3 x 12 = 603 mL

Concentration in water: 30.18 ÷ 603 = 0.050 μg/mL or 50 μg/L

(ii) Ideally the test substance should be applied as an aqueous solution into the water phase of the test system. If unavoidable, the use of low am ounts of water miscible solvents (such as acetone, ethanol) is permitted for application and distribution of the test substance, but this should not exceed

1% v/v and should not have adverse effects on microbial activity of the test system. Care should be exercised in generating the aqueous solution of the test substance - use of generator columns and premixing may be appropriate to ensure complete homogeneity. Following addition of the aqueous solution to the test system, gentle mixing of the water phase is recommended, disturbing the sediment as little as possible.

(iii) The use of formulated products is not routinely recommended as the formulation ingredients may affect the distribution of the test substance and/or transformation products between12 water and sediment phases. Studies should be conduc ted with the active ingredient (technical grade or better), not with a formulated product.

(iv) The number of incubation vessels depends on the number of sampling times (see paragraph (f)(4)(i)). A sufficient number of test systems should be included so that two systems may be sacrificed at each sampling time. Where control un its of each aquatic sediment system are employed, they should not be treated with the test substance. The control units can be used to determine the

microbial biomass of the sediment and the total organic carbon of the water and sediment at the termination of the study. Two of the control units (i.e. one control unit of each aquatic sediment) can be used to monitor the required parameters in the sediment and water during the acclimation period (see Table 1). Two additional control units have to be included if the test substance is applied by means of a solvent to measure adverse effects on the microbial activity of the test system.

(4) Test duration and sampling . (i) The duration of the experiment should normally not exceed 100 days (see paragraph (h)(9) of this guideline), and should continue until the degradation pathway and water/sediment distribution pattern are es tablished or when 90 % of the test substance has been removed by transformation and/or volatilisati on. The study should be c onducted until the decline of parent and the formation and decline of the de gradates are established. The number of sampling times should be at least six (inc luding zero time), with an optional preliminary study (see paragraph (d)(1)(vii)) being used to establish an appropriate sampling regime and the duration of the test, unless

sufficient data are available on the test substa nce from previous studies. For hydrophobic test substances, additional sampling points during the initia l period of the study may be necessary in order to determine the rate of distribution between water and sediment phases.

(ii) At appropriate sampling times, whole inc ubation vessels (in replicate) are removed for analysis. Sediment and overlying water are analyzed separately. In cases where rapid re-oxidation of anaerobic transformation products may readily occu r, anaerobic conditions should be maintained during sampling and analysis. The surface wate r should be carefully removed with minimum

disturbance of the sediment. The extraction a nd characterization of the test substance and transformation products should follow appropriate anal ytical procedures. Care should be taken to remove material that may have adsorbed to the in cubation vessel or to interconnecting tubing used to trap volatiles.

(5) Measurements and analysis.

(i) Concentration of the test substance and th e transformation products at every sampling time

in water and sediment should be measured and re ported (as a concentration and as percentage of applied). In general, transf ormation products detected at ≥ 10% of the applied radioactivity in the total water-sediment system at any sampling time should be identified unless reasonably justified otherwise. Transformation products for whic h concentrations are continuously increasing during the study should

also be considered for identifica tion, even if their concentrations do not exceed the limits given above, as this may indicate persistence. The latter s hould be considered on a case by case basis, with justifications being provided in the report. (ii) Results from gases/volatiles trapping systems (CO 2 and others, i.e., volatile organic13 compounds) should be reported at each sampling time. Mineralization rates should be reported. Nonextractable (bound) residues in sediment are to be reported at each sampling point.

(6) Calculations . (i) Total mass balance or recovery (see paragraph (e)(2)(iii)) of added radioactivity is to be calculated at every sampling tim e. Results should be reported as a percentage of added radioactivity. Distribution of radioactivity between water and sediment should be reported as concentrations and percentages, at every sampling time.

(ii) Half-life, DT 50 and, if appropriate, DT 75 and DT 90 of the test substance should be calculated along with their confidence limits (see paragraph (e)(2 )(v)). Information on the rate of dissipation of

the test substance in the water and sediment can be obtained through the use of appropriate evaluation tools. These can range from application of ps eudo-first order kinetics, empirical curve-fitting techniques which apply graphical or numerical solutions and more complex assessments using, for example, single- or multi-compartment models. Fu rther details can be obtained from the relevant published literature (see paragraphs (h)(35) through (h)(37) of this guideline).

(iii) All approaches have their strengths and w eaknesses and vary considerably in complexity. An assumption of first-order kinetics may be an ove rsimplification of the degradation and distribution processes, but when possible gives a term (the rate constant or half-life) which is easily understood and of value in simulation modelling and calculations of predicted environmental concentrations. Empirical approaches or linear transformations can resu lt in better fits of curves to data and therefore allow better estimation of half-lives, DT 50 and, if appropriate, DT 75 and DT 90 values. The use of the derived constants, however, is limited. Compartm ent models can generate a number of useful

constants of value in risk assessment that describe the rate of degradation in different compartments and the distribution of the chemical. They should also be used for estimation of rate constants for the formation and degradation of major transformation products. In all cases, the method chosen should be justified and the experimenter should demonstr ate graphically and/or statistically the goodness of

fit.

(g) Test report —The report should include the following information:

(1) Test substance . (i) Common name, chemical name, CAS number, structural formula (indicating position of the label(s) when radiolabeled material is used) and relevant physical-chemical properties.

(ii) Purity (impurities) of test substance.

(iii) Radiochemical purity of labeled chemical and molar activity (where appropriate).

(2) Reference substances . Chemical name and structure of reference substances used for the characterization and/or identification of transformation products.

(3) Test sediments and waters : (i) Location and description of aquatic sediment sampling site(s) including, if possible, contamination history.14 (ii) All information relating to the collecti on, storage (if any) and acclimation of watersediment systems.

(iii) Characteristics of the water-sediment samples as listed in Table 1.

(4) Test conditions . (i) Test system used (flow-thr ough, biometer, way of ventilation, method of stirring, water volume, mass of sediment, thickness of both water and sediment layer, dimension of test vessels, etc.).

(ii) Application of test substance to test syst em: test concentration used, number of replicates and controls mode of application of test substance (e.g. use of solvent if any), etc.

(iii) Incubation temperature.

(iv) Sampling times.

(v) Extraction methods and efficiencies as well as analytical methods and detection limits.

(vi) Methods for characterization/identification of transformation products.

(vii) Deviations from the test protocol or test conditions during the study.

(5) Results . (i) Raw data figures of representative analyses (all raw data have to be stored in the GLP-archive).

(ii) Repeatability and sensitivity of the analytical methods used.

(iii) Rates of recovery (% values for a valid study are given in paragraph (e)(2)(iii)).

(iv) Tables of results expressed as % of the applied dose and in mg/kg in water, sediment and total system (% only) for the test substance and, if appropriate, for transformation products and nonextractable radioactivity.

(v) Mass balance during and at the end of the studies.

(vi) A graphical representation of the transformation in the water and sediment fractions and in total system (including mineralization).

(vii) Mineralization rates.

(viii) Half-life, DT 50 and, if appropriate, DT 75 and DT 90 values for the test substance and, where appropriate, for transformation products includi ng confidence limits in water, sediment and in total system.15 (ix) An assessment of the transformation kinetics of the test substance and, where appropriate, the transformation products.

(x) A proposed pathway of transformation, where appropriate.

(xi) Discussion of results.

(h) References . The following references should be consulted for additional background information on this guideline:

(1) Environmental Protection Agency (1998). Sediment/water microcosm biodegradation test. Harmonised Test Guidelines (OPPTS 835.3180). EPA 712-C-98-080.

(2) Organization for Economic Cooperation and Development (1981). Test Guideline 304A: Inherent Biodegradability in Soil.

(3) DFG: Pesticide Bound Residues in Soil. Wiley-VCH (1998).

(4) Roberts, T.R. (1984): Non-extractable pesticide residues in soils and plants. Pure Appl. Chem. 56, 945-956 (IUPAC 1984).

(5) BBA-Guidelines for the examination of plant protectors in the registration process. (1990). Part IV, Section 5-1: Degradability and fate of plant protectors in the water/sediment system.Germany.

(6) Commission for registration of pesticides: Application for registration of a pesticide. (1991) Part G. Behaviour of the product and its metabolites in soil, water and air, Section G.2.1 (a). The Netherlands.

(7) MAFF Pesticides Safety Directorate (1992). Preliminary guideline for the conduct ofbiodegradability tests on pesticides in natural sediment/water systems. Ref No SC 9046. UnitedKingdom.

(8) Agriculture Canada: Environmental chemistry and fate (1987). Guidelines for registration of pesticides in Canada. Aquatic (Laboratory) - Anaerobic and aerobic. Canada. pp 35-

37.

(9) SETAC-Europe publication (1995). Procedures for assessing the environmental fate and ecotoxicity of pesticides. Ed. Dr Mark R. Lynch. SETAC-Europe, Brussels.16 (10) Organization for Economic Cooperation a nd Development. OECD Test Guidelines Programme (1995). Final Report of the OECD Workshop on Selection of Soils/sediments, Belgirate, Italy, 18-20 January 1995.

(11) Scholz, K., Fritz R., Anderson C. and Spite ller M. (1988) Degradation of pesticides in an aquatic model ecosystem. BCPC - Pests and Diseases, 3B-4, 149-158.

(12) Guth, J.A. (1981). Experimental approaches to studying the fate of pesticides in soil. In Progress in Pesticide Biochemistry (D.H. Hutson, T.R. Roberts, Eds.), Vol. 1, 85-114. J. Wiley

& Sons.

(13) Madsen, T., Kristensen, P. (1997). E ffects of bacterial inoculation and non-ionic surfactants on degradation of polycyclic aromatic hydrocarbons in soil. Environ. Toxicol. Chem. 16, 631-637.

(14) Steber, J., Wierich, P. (1987). The anaerobic degradation of detergent range fatty alcohol ethoxylates. Studies with 14 C-labelled model surfactants. Water Research 21, 661-667.

(15) Methods of Soil Analysis (1986). Part 1, Physical and Mineralogical Methods (A. Klute, Ed.). Soil Science Society of America Book Series 5.

(16) Methods of Soil Analysis (1994). Part 2. Microbiological and Biochemical Properties (R.W. Weaver, S. Angle and P. Bottomley, Eds.). Soil Science Society of America Book Series 5.

(17) Methods of Soil Analysis (1996). Part 3. Chemical Methods (D.L. Sparks, Ed.). Soil Science Society of America Book Series 5.

(18) American Public Health Association (1989). Standard Methods for Examination of Water and Wastewater (17 th edition). American Public Health Association, American Water Works Association and Water Pollution Control Federation, Washington D.C.

(19) Rowell, D.L. (1994). Soil Science: Methods and Applications. Longman Scientific & Technical, Longman Group UK Ltd, Harlow, Essex, UK (co-published in the USA with John Wiley & Sons Inc. New York).

(20) Light, T.S. (1972). Standard solution for redox potential measurements. Anal. Chemistry 44, 1038-1039.

(21) SETAC-Europe publication (1991). Guidance document on testing procedures for pesticides in freshwater mesocosms. From the Workshop “A Meeting of Experts on Guidelines for Static Field Mesocosms Tests”, 3-4 July 1991.

(22) SETAC-Europe publication (1993). Guidan ce document on sediment toxicity tests and bioassays for freshwater and marine environmen ts. From the Workshop On Sediment Toxicity17 Assessment (WOSTA), 8-10 November 1993. Eds.: I.R. Hill, P. Matthiessen and F. Heimbach.

(23) Vink, J.P.M., van der Zee, S.E.A.T.M. (1997). Pesticide biotransformation in surface waters:multivariate analyses of environmental factors at field sites. Water Research 31, 2858-

2868.

(24) Vink, J.P.M., Schraa, G., van der Zee, S.E.A.T.M. (1999). Nutrient effects on microbial transformation of pesticides in nitrifying waters. Environ. Toxicol., 329-338.

(25) Anderson, T.H., Domsch, K.H. (1985). Maintenance carbon requirements of activelymetabolising microbial populations under in-situ conditions. Soil Biol. Biochem. 17, 197-203.

(26) ISO-14240-2. (1997). Soil quality - Determination of soil microbial biomass - Part 2: Fumigation-extraction method.

(27) ISO/DIS 5667-12(1994) Water quality - Sampling - Part 12: Guidance on sampling of

bottom sediments.

(28) Beelen, P. van and F. van Keulen. (1990). The Kinetics of the Degradation of

Chloroform and Benzene in Anaerobic Sediment fr om the River Rhine. Hydrobiol. Bull. 24(1), 13-

21.

(29) Shelton, D.R. and Tiedje, J.M. (1984). General method for determining anaerobic biodegradation potential. App. Environ. Microbiol. 47, 850-857.

(30) Birch, R.R., Biver, C., Campagna, R., Gle dhill, W.E., Pagga, U., Steber, J., Reust, H. and Bontinck, W.J. (1989). Screening of chemi cals for anaerobic biodegradation. Chemosphere 19,

1527-1550.

(31) Pagga, U. and Beimborn, D.B. (1993). Anaerobic biodegradation tests for organic compounds. Chemoshpere 27, 1499-1509.

(32) Nuck, B.A. and Federle, T.W. (1986). A batch test for assessing the mineralisation of

14 C- radiolabelled compounds under realistic anaerobic conditions. Environ. Sci. Technol. 30,

3597-3603.

(33) Environmental Protection Agency (1998). Anaerobic biodegradability of organic

chemicals. OPPTS Harmonised Test Guideline 835.3400. EPA 712-C-98-090.

(34) Sijm, R.T.H.M., Haller, M., and Schrap, S.M. (1997). Influence of storage on sediment characteristics and drying sediment on so rption coefficients of organic contaminants. Bulletin Environ. Contam. Toxicol. 58, 961-968.18 (35) Timme, G., Frehse H. and Laska V. ( 1986) Statistical interpretation and graphic representation of the degradational behaviour of pesticide residues II. Pflanzenschutz - Nachrichten Bayer, 39, 187 - 203.

(36) Timme, G., Frehse, H. (1980) Statistical interpretation and graphic representation of the degradational behaviour of pesticide residues I. Pflanzenschutz - Nachrichten Bayer, 33, 47 -

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(37) Carlton, R.R. and Allen, R. (1994). The use of a compartment model for evaluating the fate of pesticides in sediment/water system s. Brighton Crop Protection Conference - Pest and Diseases, pp 1349-1354.