natgillin/translations-raw huggingface dataset:
It is recommended that the BAF is expressed both as a function of total wet weight, total dry weight, and, when required (e.g. for highly lipophilic substances) as a function of the lipid content and the TOC of the sediment.
1,1 – 1,4
at steady state or at day 28mean
OECD (1984), Activated sludge, Respiration inhibition test, Test Guideline No.
Determine the kinetic bioaccumulation factor (BAFK) as the ratio ks/ke.
209, Guidelines for the testing of chemicals, OECD, Paris.
The elimination constant (ke) is usually determined from the elimination curve (i.e. a plot of the concentration of the test substance in the worms during the elimination phase).
ISO (2007).
The uptake rate constant ks is then calculated from the uptake curve kinetics.
Bealing, D. J. (2003).
The preferred method for obtaining BAFK and the rate constants, ks, and ke, is to use non-linear parameter estimation methods on a computer (see Appendix 2).
Painter, H A, Jones K (1963).
If the elimination is obviously not first-order, then more complex models should be employed (25)(27)(52).
Painter, H. A. (1986).
The biota-sediment accumulation factor (BSAF) is determined by normalising the BAFK for the worm lipid content and the sediment total organic carbon content.
Robra, B. (1976).
The results should be interpreted with caution where measured concentrations of test concentrations occur at levels close to the detection limit of the analytical method used.
Fiebig S. and Noack, U. (2004).
Clearly defined uptake and elimination curves are an indication of good quality bioaccumulation data.
The use of copper(II)sulphate pentahydrate as reference substance in the activated sludge respiration inhibition test – acc. to the OECD guideline 209.
Generally the confidence limits for the BAF values from well-designed studies should not exceed 25 % (5).
ISO (1995).
The test report must include the following information.
ISO 10634 Water Quality – Guidance for the preparation and treatment of poorly water-soluble organic compounds for the subsequent evaluation of their biodegradability in aqueous medium, International Organization for Standardization.
physical nature and, physicochemical properties e.g. log Kow, water solubility;
ASTM International.
chemical identification data;
US EPA – United States Environmental Protection Agency.
source of the test substance, identity and concentration of any solvent used;
AFNOR – Association Française de Normalisation.
if radiolabelled, the precise position of the labelled atoms, the specific radioactivity, and the percentage of radioactivity associated with impurities.
SSI – Swedish Standards Institute.
scientific name, strain, source, any pre-treatment, acclimation, age, size-range, etc..
Water quality – Determination of growth inhibition (7-d) Lemna minor, duckweed.
type and characteristics of illumination used and photoperiod(s);
Environment Canada.
test design (e.g. number, material and size of test chambers, water volume, sediment mass and volume, water volume replacement rate (for flow-through or semi-static procedures), any aeration used before and during the test, number of replicates, number of worms per replicate, number of test concentrations, length of uptake and elimination phases, sampling frequency);
Sims I., Whitehouse P. and Lacey R. (1999) The OECD Lemna Growth Inhibition Test.
method of test substance preparation and application as well as reasons for choosing a specific method;
WRc plc – Environment Agency.
the nominal test concentrations;
International Organisation for Standardisation.
source of the constituents of the artificial water and sediment or — if natural media are used — origin of the water and the sediment, description of any pre-treatment, results of any demonstration of the ability of the test animals to live and/or reproduce in the media used, sediment characteristics (pH and ammonia of the pore water (natural sediments), organic carbon content (TOC), particle size distribution (percent sand, silt, and clay), percent water content, and any other measurements made) and water characteristics (pH, hardness, conductivity, temperature, dissolved oxygen concentration, residual chlorine levels (if measured), and any other measurements made);
Water Quality – Determination of the Toxic Effect of Water Constituents and Waste Water to Duckweed (Lemna minor) – Duckweed Growth Inhibition Test.
the nominal and measured dry weight in % of wet weight (or dry weight-to-wet weight ratio) of the artificial sediment;
Walbridge C. T. (1977).
the measured dry weight in % of wet weight (or dry weight-to-wet weight ratio) for field sediments;
Environmental Research Laboratory – Duluth, Minnesota 55804
water quality within the test chambers as characterised by temperature, pH, ammonium, total hardness, and dissolved oxygen concentration;
Lockhart W.
detailed information on the treatment of water, sediment, and worm samples, including details of preparation, storage, spiking procedures, extraction, and analytical procedures (and precision) for the test substance and lipid content, and recoveries of the test substance.
Hydrobiologia, 118/119, 353 – 359.
mortality of the control worms and the worms in each test chamber and any observed sublethal effects including abnormal behaviour (e.g., sediment avoidance, presence or absence of fecal pellets, lack of reproduction);
Huebert, D.B. and Shay J.M.
the measured dry weight in % of wet weight (or dry weight-to-wet weight ratio) of the sediment and the test organisms (useful for normalisation);
Christensen, E.R.,, Nyholm, N. (1984):
the lipid content of the worms;
Bruce R.D. and Versteeg D.J.
curves showing the uptake and elimination kinetics of the test substance in the worms, and the time to steady state;
Brain P. and Cousens R. (1989).
Ca, Cs and Cw (with standard deviation and range, if appropriate) for all sampling times (Ca expressed in g kg– 1 wet and dry weight of whole body, Cs expressed in g kg– 1 wet and dry weight of sediment, and Cw in mg l– 1).
Zdroje druhov Lemna
If a biota-sediment accumulation factor (BSAF; see Appendix 1 for definition) is required (e.g. for comparison of results from two or more tests performed with animals of differing lipid content), Ca should additionally be expressed as g kg– 1 lipid content of the organism, and Cs should be expressed as g kg– 1 organic carbon (OC) of the sediment;
USA
BAF (expressed in kg wet sediment kg– 1 wet worm), sediment uptake rate constant ks (expressed in g wet sediment kg– 1 of wet worm d– 1), and elimination rate constant ke (expressed in d– 1);
ŠVÉDSKO
BSAF (expressed in kg sediment OC kg– 1 worm lipid content) may be reported additionally;
NEMECKO
Non-eliminated residues (NER) at end of elimination phase;
Hillman, W.S.
if measured:
Landolt, E. (1986).
percentages of parent substance, degradation products, and bound residues (i.e. the percentage of test substance that cannot be extracted with common extraction methods) detected in the test animals;
Björndahl, G. (1982).
methods used for statistical analyses of the data.
Wang, W.
Evaluation of results
Hodnota pH sa nastaví na 6,5 ± 0,2 pridaním 0,1 alebo 1 mol HCl alebo NaOH a objem sa doplní do jedného litra deionizovanou vodou.
compliance of the results with the validity criteria as listed in paragraph 21;
Rastové médium 20X AAP
unexpected or unusual results, e.g. incomplete elimination of the test substance from the test animals;
Zásobné roztoky sa pripravia v sterilnej destilovanej alebo deionizovanej vode.
in such cases results from any preliminary study may provide useful information.
V týchto podmienkach budú mať zásobné roztoky čas použiteľnosti minimálne 6 až 8 týždňov.
Artificial sediment, or formulated, reconstituted or synthetic sediment, is a mixture of materials used to mimic the physical components of a natural sediment.
(I. Sims, P. Whitehouse a R. Lacey.
Bioaccumulation is the increase in concentration of the test substance in or on an organism relative to the concentration of the test substance in the surrounding medium.
(1999) The OECD Lemna Growth Inhibition Test.
Bioaccumulation results from both bioconcentration and biomagnification processes (see below).
Development and Ring-testing of draft OECD Test Guideline.
The bioaccumulation factor (BAF) at any time during the uptake phase of this bioaccumulation test is the concentration of test substance in/on the test organism (Ca in g kg– 1 wet or dry weight) divided by the concentration of the substance in the surrounding medium (Cs as g kg– 1 of wet or dry weight of sediment).
R&D Technical Report EMA 003.
In order to refer to the units of Ca and Cs, the BAF has the units of kg sediment kg– 1 worm (15).
WRc plc – Environment Agency.)
Bioaccumulation factors calculated directly from the ratio of the sediment uptake rate constant divided by the elimination rate constants (ks and ke, respectively — see below) are termed kinetic bioaccumulation factor (BAFK).
190; 84
Bioconcentration is the increase in concentration of the test substance in or on an organism, resulting exclusively from uptake via the body surface, relative to the concentration of the test substance in the surrounding medium.
Hodnota pH by mala byť 5,5 ± 0,2 (upraví sa pridaním minimálneho objemu roztoku NaOH alebo HCl).
Biomagnification is the increase in concentration of the test substance in or on an organism, resulting mainly from uptake from contaminated food or prey, relative to the concentration of the test substance in the food or prey.
Doplní sa vodou do 1000 ml.
Biomagnification can lead to a transfer or accumulation of the test substance within food webs.
22 °C ± 10 °C,
The biota-sediment accumulation factor (BSAF) is the lipid-normalised steady state concentration of test substance in/on the test organism divided by the organic carbon-normalised concentration of the substance in the sediment at steady state.
70 % ± 25 %,
Ca is then expressed as g kg– 1 lipid content of the organism, and Cs as g kg– 1 organic content of the sediment.
Počet a rozstup hodnôt koncentrácie alebo dávky by mal byť dostatočný na vytvorenie spoľahlivého vzťahu dávky a účinku a príslušnej regresnej rovnice, ako aj na stanovenie odhadu hodnoty ECx alebo ERx.
The conditioning period is used to stabilise the microbial component of the sediment and to remove e.g. ammonia originating from sediment components; it takes place prior to spiking of the sediment with the test substance.
Zvolené koncentrácie/dávky by mali zahŕňať hodnoty ECx alebo ERx, ktoré treba určiť.
The elimination rate constant (ke) is the numerical value defining the rate of reduction in the concentration of the test substance in/on the test organism, following the transfer of the test organisms from a medium containing the test substance to a chemical-free medium;
Schrader G., Metge K., and Bahadir M. (1998).
ke is expressed in d– 1.
International Organisation of Standards.
The equilibration period is used to allow for distribution of the test substance between the solid phase, the pore water and the overlying water;
Soil Quality -- Determination of the Effects of Pollutants on Soil Flora – Part 1:
it takes place after spiking of the sediment with the test substance and prior to addition of the test organisms.
Soil Quality -- Determination of the Effects of Pollutants on Soil Flora – Part 2:
The octanol-water partitioning coefficient (Kow) is the ratio of substance's solubility in n-octanol and in water at equilibrium, also sometimes expressed as Pow.
American Standard for Testing Material (ASTM).
The logarithm of Kow (log Kow) is used as an indication of a substance's potential for bioaccumulation by aquatic organisms.
U.S.
The organic carbon-water partitioning coefficient (Koc) is the ratio of a substance's concentration in/on the organic carbon fraction of a sediment and the substance's concentration in water at equilibrium.
US EPA.
Overlying water is the water lying on top of the sediment in the test vessel.
Background – Non-target Plant Testing;
A plateau or steady state is defined as the equilibrium between the uptake and elimination processes that occur simultaneously during the exposure phase.
AFNOR, X31-201.
The steady state is reached in the plot of the BAF at each sampling period against time when the curve becomes parallel to the time axis and three successive analyses of BAF made on samples taken at intervals of at least two days are within 20 % of each other, and there are no statistically significant differences among the three sampling periods.
Boutin, C., Freemark, K.E. and Keddy, C.J.
For test substances which are taken up slowly, more appropriate intervals would be seven days (5).
Forster, R., Heimbach, U., Kula, C., and Zwerger, P. (1997).
The sediment uptake rate constant (ks) is the numerical value defining the rate of increase in the concentration of the test substance in/on the test organism resulting from uptake from the sediment phase. ks is expressed in g sediment kg– 1 of worm d– 1.
Effects of Plant Protection Products on Non-Target Organisms – A contribution to the Discussion of Risk Assessment and Risk Mitigation for Terrestrial Non-Target Organisms (Flora and Fauna).
Spiked sediment is sediment to which test substance has been added.
Hale, B., Hall, J.C., Solomon, K., and Stephenson, G. (1994).
The steady state bioaccumulation factor (BAFss) is the BAF at steady state and does not change significantly over a prolonged period of time, the concentration of the test substance in the surrounding medium (Cs as g kg– 1 of wet or dry weight of sediment) being constant during this period of time.
Soil Texture Classification (US and FAO systems):
The uptake or exposure phase is the time during which the test organisms are exposed to the test substance.
Audus, L.J.
The main endpoint of a bioaccumulation test is the bioaccumulation factor, BAF.
Beetsman, G.D., Kenney, D.R. and Chesters, G. (1969).
The measured BAF can be calculated by dividing the concentration of the test substance in the test organism, Ca, by the concentration of the test substance in the sediment, Cs, at steady state.
Dieldrin uptake by corn as affected by soil properties, J. Agro.
If the steady state is not reached during the uptake phase, the BAF is calculated in the same manner for day 28.
McKelvey, R.A., Wright, J.P., Honegger, J.L. and Warren, L.W.
However, it should be noted whether the BAF is based on steady state concentrations or not.
Boutin, C.;
The preferred means for obtaining the kinetic bioaccumulation factor (BAFK), the sediment uptake rate constant (ks) and the elimination rate constant (ke) is to use non-linear parameter estimation methods on a computer.
Boutin, C., and Rogers, C.A.
Given the time series of average accumulation factors (Ca, mean values of each sampling date/Cs, mean values of each sampling date = AF) of the uptake phase based on worm and sediment wet weight, and the model equation
Patterns of sensitivity of plant species to various herbicides – An analysis with two databases.
[equation 1]
Boutin, C. and Harper, J.L.
where AF(t) is the ratio of concentration of the test substance in worms and its concentration in the sediment at any given time point (t) of the uptake phase, these computer programs calculate values for BAFK, ks and ke.
Boutin, C., Lee, H.-B., Peart, T.E., Batchelor, S.P. and Maguire, R.J.. (2000).
When steady state is reached during the uptake phase (i.e. t = ∞), equation 1 may be reduced to:
Hatzios, K.K. and Penner, D. (1985).
[equation 2]
Hamill, P.B., Marriage, P.B. and G. Friesen.
uptake rate constant in tissue [g sediment kg– 1 of worm d– 1]
Frans, R.E. and Talbert, R.E.
elimination rate constant [d– 1]
Bruce, R.D. and Versteeg, D. J.(1992).
Then ks/ke × Cs is an approach to the concentration of the test substance in the worm tissue at steady state (Ca,ss).
0,09 – 0,17 (4, 19)
The Biota-Sediment Accumulation Factor (BSAF) should be calculated as follows:
14 – 21 (100 %) (14)
where foc is the fraction of sediment organic carbon, and flip is the fraction of worm lipid, both based either on dry weight, or on wet weight.
2,4 – 4,9 (14, 19)
Given a time series of concentration values, the elimination kinetics can be modelled using the following model equations and a computer calculation based non-linear parameter estimation method.
0,85 – 1,2 (14, 19)
The mean measured body residue at the end of the uptake phase is recommended as the default starting point.
0,06 – 0,08 (4, 14)
The value modeled/estimated from the uptake phase should only be used, e.g. if the measured value deviates significantly from the modelled body residue.
14 – 21
See also paragraph 50 for alternative pre-exposure of worms designated for elimination;
25 – 61 (14, 29)
with this approach, samples of these pre-exposed worms on day 0 of the elimination phase are thought to provide a realistic body residue to start the elimination kinetics with.
10 – 20 (6, 21)
If the data points plotted against time indicate a constant exponential decline of the test substance concentration in the animals, a one-compartment model (equation 4) can be used to describe the time course of elimination.
10 – 20
[equation 3]
10 – 20 (6, 10)
Elimination processes sometimes appear to be biphasic, showing a rapid decline of Ca during the early phases, that changes to a slower loss of test substances in the later phases of the elimination (8)(19)(25)).
14 – 18
The two phases can be interpreted by the assumption, that there are two different compartments in the organism, from which the test substance is lost with different velocity.
0,9 – 1,6
In these cases specific literature should be studied (15)(16)(17)(25).
7 – 7,5 (14, 30)
A two-compartment elimination is described e.g. by the following equation (25):
0,45 – 2,28 (14, 29)
[equation 4]
0,5 – 0,7 (14, 19, 29)
A and B represent the size of the compartments (in percent of overall tissue residue), where A is the compartment with rapid loss of substance, and B the compartment with slow loss of test substance.
0,52 – 0,6 (14, 30)
The sum of A and B equals 100 % of the whole animal compartment volume at steady state. ka and kb represent the corresponding elimination constants [d– 1].
10 – 20 (21)
If the two compartment model is fitted to the depuration data, the uptake rate constant ks may be determined as follows (53)(54):
10 – 20 (7, 21)
[equation 5]
4 – 5 (14, 30)
Nevertheless, these model equations should be used with caution, especially when changes in the test substance's bioavailability occur during the test (42).
14 – 28
As an alternative to the model equations described above, the kinetics (ks and ke) may also be calculated in one run by applying the first order kinetics model to all data from both the uptake and elimination phase together.
1,53 – 2,2 (16, 19)
For a description of a method that may allow for such a combined calculation of uptake and elimination rate constants, references (55), (56) and (57) may be consulted.
0 – 10 (10, 19)
The Non-Eliminated Residues (NER) should be calculated as a secondary endpoint by multiplying the ratio of the average concentration in the worms (Ca) on day 10 of the elimination phase and the average concentration in the worms (Ca) at steady state (day 28 of uptake phase) by 100:
5 – 8 (4, 14, 29)
Example of a Sampling Schedule for a 28-day Bioaccumulation Test
0 – 2 (4, 29)
Uptake phase (including a 4 d- equilibration phase)
1,8 – 2,5 (14)
Activities
3,6 – 7 (14, 29)
Preparation of peat suspension for sediment;
2,1 – 2,3 (14, 19)
conditioning of the suspension for 48 h;
1,3 – 1,5 (4, 14, 19)
Spiking of the sediment or sediment fraction;
0,4 – 0,5 (4, 14, 19)
mixing of all sediment constituents;
1,5 – 2 (14, 19, 29)
removing sediment samples of treated and solvent control sediment for determination of test substance concentration;
41 – 56 (19, 29)
addition of overlying water;
0,8 – 1,5 (14, 19)
incubation at test conditions (equilibration phase);
7 – 9 (14, 19)
Separation of the test organisms from the culture for acclimatisation;
PO (4, 22 – 26)
of water quality (see paragraph 52);
0,5 – 0,6 (14, 19)
removing replicates for taking samples of water and sediment for determination of test substance concentration;
3 (19)
randomised distribution of the worms to the test chambers;
Pterophylla – Native Plants & Seeds
retaining of sufficient sub-samples of worms for determination of analytical background values;
Baskin, C.C.
controlling air supply, if closed test system is used;
Blackburn, L.G.
Remove replicates for sampling;
Boutin, C., Lee, H-B., Peart, T., Batchelor, P.S., & Maguire, R.J.
controlling air supply, worm behaviour, water quality (see paragraph 56);
Boutin, C., Elmegaard, N., & Kjaer, C. 2004.
taking water, sediment and worm samples for determination of test substance concentration;
Breeze, V., Thomas, G., & Butler, R. 1992.
4 - 6
Clapham, A.R., Tutin, T.G., & Warburg, E.F.
Same as day 2;
Clay, P.A.
compensate evaporated water if necessary;
Cole, J.F.H.
8 - 13
Fiely, M.
15 - 20
(Ernst Conservation Seeds).
22 - 27
Fletcher, J.S., Johnson, F.L., & McFarlane, J.C. 1990.
measurement of water quality (see paragraph 52);
Fletcher, J.S., Pfleeger, T.G., Ratsch, H.C., & Hayes, R. 1996.
end of uptake phase;
Flynn, S., Turner, R.M., and Dickie, J.B.
retaining of sufficient subsamples of worms for determination of analytical background values, wet and dry weight, and lipid content;
Franzaring, J., Kempenaar, C., & van der Eerden, L.J.M.
transfer worms from remaining exposed replicates to vessels containing clean sediment for elimination phase (no gut-purging);
Gleason, H.A.
sampling of water, sediment and worms from solvent controls; sampling of trapping solutions, if installed.
Grime, J.P.
Pre-exposure activities (equilibration phase) should be scheduled taking into account the properties of the test substance.
Grime, J.P., Mason, G., Curtis, A.V., Rodman, J., Band, S.R., Mowforth, M.A.G., Neal, A.M., & Shaw, S. 1981.
If required, conditioning of the prepared sediment under overlying water at 20 ± 2 °C for 7 days;
Grime, J.P., Hodgson, J.G., & Hunt, R. 1988.
in this case, earlier preparation of the sediment!
Kjaer, C. 1994.
Activities described for day 2 should be performed daily (at least on workdays).
Klingaman, T.E., King, C.A., & Oliver, L.R.
Elimination phase
Marrs, R.H., Williams, C.T., Frost, A.J., & Plant, R.A.
Mixing of all sediment constituents;
Marrs, R.H., Frost, A.J., & Plant, R.A.
incubation at test conditions;
Marrs, R.H., Frost, A.J., Plant, R.A., & Lunnis, P. 1993.
0 (day 28 of uptake phase)
Marrs, R.H.
Measurement of water quality (see paragraph 52);
Marshall, E.J.P.
transfer worms from remaining exposed replicates to vessels containing clean sediment;
McKelvey, R.A., Wright, J.P., & Honegger, J.L.
after 4 - 6 h removing replicates for taking samples of water, sediment and worms for determination of test substance concentration;
Morton, S.
controlling air supply, worm behaviour, water quality (see paragraph 52);
(Herbiseed).
8 - 9
USDA, NRCS.
end of elimination phase;
USEPA.
sampling of water, sediment and worms from solvent controls;
Webster, R.H.
sampling of trapping solutions, if installed.
White, A. L. & Boutin, C.
Preparation of the sediment prior to start of elimination phase should be done in the same manner as before the uptake phase.
(National Wildlife Research Centre, Environment Canada).
Some physical-chemical characteristics of an acceptable dilution water
Zwerger, P. & Pestemer, W.
< 2μg/l
350 ppm ± 50 ppm,
COMPOSITION OF THE RECOMMENDED RECONSTITUTED WATER
Nosič sa nastrieka na malé množstvo, napríklad 2,5 g, jemného kremenného piesku, alebo sa s ním zmieša.
The sum of the calcium and magnesium ions in this solution is 2,5 mmol/l.
Alternatívne sa môžu použiť viacnásobné U-testy, napríklad Bonferroniho U-test podľa Holma (29), alebo v prípade, keď tieto údaje vykazujú heteroscedasticitu, ale inak sú v súlade so základným monotónnym priebehom krivky závislosti dávka-odpoveď, môže sa použiť iný neparametrický test [napr. Jonckheereho-Terpstrov (30) (31) alebo Shirleyho (32) (33)], pričom vo všeobecnosti sú tieto testy uprednostňované pred t-testami s nerovnakou varianciou (pozri tiež náčrt v dodatku 7).
The pH of an acceptable dilution water should be in the range of 6 - 9.
Römbke, J. (1989).
Artificial sediment — preparation and storage recommendations
Entwicklung eines Reproduktionstests an Bodenorganismen – Enchytraeen.