natgillin/translations-raw huggingface dataset:
B. Beek, S. Boehling, U. Bruckmann, C. Franke, U. Joehncke og G. Studinger (2000).
The biota-sediment accumulation factor (BSAF) is determined by normalising the BAFK for the worm lipid content and the sediment total organic carbon content.
A. Spacie og J.L.
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.
D.W.
Clearly defined uptake and elimination curves are an indication of good quality bioaccumulation data.
T.B. Reynoldson, S.P.
Generally the confidence limits for the BAF values from well-designed studies should not exceed 25 % (5).
M.R.
physical nature and, physicochemical properties e.g. log Kow, water solubility;
C.J.
chemical identification data;
T.L.
source of the test substance, identity and concentration of any solvent used;
R.N. Hooftman, K. van de Guchte og C.J.
if radiolabelled, the precise position of the labelled atoms, the specific radioactivity, and the percentage of radioactivity associated with impurities.
C. Franke (1996).
scientific name, strain, source, any pre-treatment, acclimation, age, size-range, etc..
R.C. Randall, H. Lee II, R.J.
type and characteristics of illumination used and photoperiod(s);
S. Zok, G. Görge, W.
the nominal and measured dry weight in % of wet weight (or dry weight-to-wet weight ratio) of the artificial sediment;
R. Nagel (1988).
the measured dry weight in % of wet weight (or dry weight-to-wet weight ratio) for field sediments;
(1988).
water quality within the test chambers as characterised by temperature, pH, ammonium, total hardness, and dissolved oxygen concentration;
M.P.M. Janssen, A. Bruins, T.H.
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.
T.C.
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);
I. Sterenborg, N.A. Vork, S.K.
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);
B. Wachs (1967).
the lipid content of the worms;
B.G. Oliver (1987).
curves showing the uptake and elimination kinetics of the test substance in the worms, and the time to steady state;
P.M. Chapman, M.A.
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).
R.J. Aston, K. Sadler og A.G.P.
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;
C.J. Roghair, A. Buijze, M.P.A.
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);
Tilpasningen omfatter 20 testmetoder, én ny metode til fastlæggelse af en fysisk-kemisk egenskab, 11 nye testmetoder og tre opdaterede testmetoder til vurdering af økotoksicitet og fem nye testmetoder til vurdering af skæbne og adfærd i miljøet.
BSAF (expressed in kg sediment OC kg– 1 worm lipid content) may be reported additionally;
Formand
Non-eliminated residues (NER) at end of elimination phase;
Cvand
if measured:
C. V. Eadsforth og P. Moser (1983), Assessment of Reverse Phase Chromatographic Methods for Determining Partition Coefficients, Chemosphere, 12, 1459.
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;
Klein, W.
methods used for statistical analyses of the data.
Kördel, M. Weiss og H. J. Poremski (1988), Updating of the OECD Test Guideline 107 Partition Coefficient n-Octanol-Water, OECD Laboratory Intercomparison Test on the HPLC Method, Chemosphere, 17, 361.
Evaluation of results
C. V. Eadsforth (1986), Application of Reverse H.P.L.C. for the Determination of Partition Coefficient, Pesticide Science, 17, 311.
compliance of the results with the validity criteria as listed in paragraph 21;
H. Ellgehausen, C. D'Hondt og R. Fuerer (1981), Reversed-phase chromatography as a general method for determining octan-1-ol/water partition coefficients, Pesticide Science, 12, 219.
unexpected or unusual results, e.g. incomplete elimination of the test substance from the test animals;
B. McDuffie (1981), Estimation of Octanol Water Partition Coefficients for Organic Pollutants Using Reverse Phase High Pressure Liquid Chromatography, Chemosphere, 10, 73.
in such cases results from any preliminary study may provide useful information.
OECD (2000), Guideline for Testing of Chemicals — Partition Coefficient (n-octanol/water):
Artificial sediment, or formulated, reconstituted or synthetic sediment, is a mixture of materials used to mimic the physical components of a natural sediment.
pH-metric Method for Ionisable Substances, Draft Guideline, november 2000.
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.
OSPAR (1995), »Harmonised Offshore Chemicals Notification Format (HOCFN) 1995«, Oslo and Paris Conventions for the Prevention of Marine Pollution Programmes and Measures Committee (PRAM), Annex 10, Oviedo, 20.-24. februar 1995.
Bioaccumulation results from both bioconcentration and biomagnification processes (see below).
M. Thatcher, M. Robinson, L. R. Henriquez og C. C. Karman (1999), An User Guide for the Evaluation of Chemicals Used and Discharged Offshore, A CIN Revised CHARM III Report 1999, Version 1.0, 3, august.
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).
E. A. Vik, S. Bakke og K. Bansal (1998), Partitioning of Chemicals, Important Factors in Exposure Assessment of Offshore Discharges, Environmental Modelling & Software Vol. 13, s. 529-537.
In order to refer to the units of Ca and Cs, the BAF has the units of kg sediment kg– 1 worm (15).
L. O. Renberg, S. G. Sundstroem og K. Sundh-Nygård (1980), Partition coefficients of organic chemicals derived from reversed-phase thin-layer chromatography.
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).
Evaluation of methods and application on phosphate esters, polychlorinated paraffins and some PCB-substitutes, Chemosphere, 9, 683.
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.
E. Hammers, G. J. Meurs og C. L. De-Ligny (1982), Correlations between liquid chromatographic capacity ratio data on Lichrosorb RP-18 and partition coefficients in the octanol-water system, J. Chromatography 247, 1.
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.
J. E. Haky og A. M. Young (1984), Evaluation of a simple HPLC correlation method for the estimation of the octanol-water partition coefficients of organic compounds, J. Liq.
Biomagnification can lead to a transfer or accumulation of the test substance within food webs.
Chromatography, 7, 675.
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.
S. Fujisawa og E. Masuhara (1981), Determination of Partition Coefficients of Acrylates Methacrylates and Vinyl Monomers Using High Performance Liquid Chromatography, Journal of Biomedical Materials Research, 15, 787.
Ca is then expressed as g kg– 1 lipid content of the organism, and Cs as g kg– 1 organic content of the sediment.
A. J. Leo, dir. (1982), Log P and Parameter Database:
The elimination phase is the time, following the transfer of the test organisms from a contaminated medium to a medium free of the test substance, during which the elimination (or the net loss) of the substance from the test organisms is studied.
R. F. Rekker og H. M. de Kort (1979), The hydrophobic fragmental constant:
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;
An extension to a 1000 data point set, Eur. J. Med.
ke is expressed in d– 1.
Chim.
The equilibration period is used to allow for distribution of the test substance between the solid phase, the pore water and the overlying water;
Ther, 14, 479.
it takes place after spiking of the sediment with the test substance and prior to addition of the test organisms.
G. E. Berendsen, P. J. Schoenmakers, L. de Galan, G. Vigh, Z. Varga-Puchony og J. Inczédy (1980), On determination of hold-up time in reversed-phase liquid chromatography, J. Liq.
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.
Chromato, 3, 1669.
The logarithm of Kow (log Kow) is used as an indication of a substance's potential for bioaccumulation by aquatic organisms.
J. Lyman, W.
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.
F. Reehl, D. H. Reehl og D. H. Rosenblatt (ed.), Handbook of Chemical Property Estimation Methods, McGraw-Hill, New York (1982).
Overlying water is the water lying on top of the sediment in the test vessel.
J. Dunn, J. H. Block og R. S. Pearlman (ed.), Partition Coefficient, Determination and Estimation, Pergamon Press, Elmsford (New York) and Oxford (1986),
A plateau or steady state is defined as the equilibrium between the uptake and elimination processes that occur simultaneously during the exposure phase.
C. Hansch og A. J. Leo Substituent Constants for Correlation Analysis in Chemistry and Biology, John Wiley, New York (1979).
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.
Leo, C. Hansch og D. Elkins (1971), Partition coefficients and their uses, Chemical.
For test substances which are taken up slowly, more appropriate intervals would be seven days (5).
Reviews, 71, 525.
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.
Toshio Fujita, Junkichi Iwasa og Corwin Hansch (1964), A New Substituent Constant, π, Derived from Partition Coefficients, J. Amer. Chem.
Spiked sediment is sediment to which test substance has been added.
Soc, 86, 5175.
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.
R. F. Rekker, The Hydrophobic Fragmental Constant, Pharmacochemistry Library, Vol. 1, Elsevier, New York (1977).
The uptake or exposure phase is the time during which the test organisms are exposed to the test substance.
Til visse formål kan det være nødvendigt at modificere substratet, f.eks. ved testning af metaller og chelaterende midler, eller når testning finder sted ved afvigende pH-værdier.
The main endpoint of a bioaccumulation test is the bioaccumulation factor, BAF.
Modificerede substrater skal beskrives i detaljer og deres anvendelse begrundes (3)(4).
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.
Der lægges en jævn linje gennem datapunkterne, enten i fri hånd eller med computerinterpolation, for at få et første indtryk af sammenhængen mellem koncentration og respons, hvorefter der fortsættes med en mere dybtgående metode, fortrinsvis en computerbaseret statistisk metode.
If the steady state is not reached during the uptake phase, the BAF is calculated in the same manner for day 28.
Den Internationale Standardiseringsorganisation (1993), ISO 8692 Water quality — Algal growth inhibition test.
However, it should be noted whether the BAF is based on steady state concentrations or not.
Den Internationale Standardiseringsorganisation (1998), ISO/DIS 14442, Water quality — Guidance for algal growth inhibition tests with poorly soluble materials, volatile compounds, metals and waster water.
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.
OECD (2000), Guidance Document on Aquatic Toxicity Testing of Difficult Substances and Mixtures, Environmental Health and Satety Publitations, Series on Testing and Assessment No. 23, Organisationen for Økonomisk Samarbejde og Udvikling, Paris.
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
Den Internationale Standardiseringsorganisation (1998), ISO 5667-16 Water quality — Sampling — Part 16:
[equation 1]
P. Mayer, R. Cuhel og N. Nyholm (1997), A simple in vitro fluorescence method for biomass measurements in algal growth inhibition tests, Water Research 31:
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.
R. E. Slovacey og P. J. Hanna (1997), In vivo fluorescence determinations of phytoplancton chlorophyll, Limnology & Oceanography 22:
When steady state is reached during the uptake phase (i.e. t = ∞), equation 1 may be reduced to:
S. L. Simpson, M. G. E. Roland, J. L. Stauber og G. E. Batley (2003), Effect of declining toxicant concentrations on algal bioassay endpoints, Environ.
[equation 2]
Toxicol.
uptake rate constant in tissue [g sediment kg– 1 of worm d– 1]
E. R. Christensen og N. Nyholm (1984), Ecotoxicological Assays with Algae:
elimination rate constant [d– 1]
Weibull Dose-Response Curves, Env.
Then ks/ke × Cs is an approach to the concentration of the test substance in the worm tissue at steady state (Ca,ss).
Sci.
The Biota-Sediment Accumulation Factor (BSAF) should be calculated as follows:
Environ.
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.
R. D. Bruce og D. J. Versteeg (1992), A statistical procedure for modelling continuous toxicity data, Environ.
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.
Toxicol.
The mean measured body residue at the end of the uptake phase is recommended as the default starting point.
OECD (2006), Current Approaches in the Statistical Analysis of Ecotoxicity Data:
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.
A Guidance to Application, Organisationen for Økonomisk Samarbejde og Udvikling, Paris.
See also paragraph 50 for alternative pre-exposure of worms designated for elimination;
C. W.
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.
Dunnett (1955), A multiple comparisons procedure for comparing several treatments with a control, J. Amer. Statist.
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.
, An interpolation estimate for chronic toxicity:
[equation 3]
National Effluent Toxicity Assessment Center Technical Report 05-88, US EPA, Duluth, MN.
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)).
C. W.
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.
Dunnett (1964), New tables for multiple comparisons with a control, Biometrics 20:
In these cases specific literature should be studied (15)(16)(17)(25).
D. A. Williams (1971), A test for differences between treatment means when several dose levels are compared with a zero dose control, Biometrics 27:
A two-compartment elimination is described e.g. by the following equation (25):
D. A. Williams (1972), The comparison of several dose levels with a zero dose control, Biometrics 28:
[equation 4]
N. R. Draper og H. Smith (1981), Applied Regression Analysis, second edition, Wiley, New York.
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.
P. Brain og R. Cousens (1989), An equation to describe dose-responses where there is stimulation of growth at low doses, Weed Research, 29, 93-96.
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].
Biomasse er tørvægten af levende materiale, som er til stede i en population, i et givet volumen, f.eks. mg alger/liter testopløsning.
If the two compartment model is fitted to the depuration data, the uptake rate constant ks may be determined as follows (53)(54):
»Biomasse« defineres sædvanligvis som masse, men skal i denne test forstås som masse pr. volumenenhed.
[equation 5]
I denne test anvendes typisk målinger af surrogater for biomasse som f.eks. celletal, fluorescens mv., hvorfor betegnelsen »biomasse« ligeledes dækker disse surrogatmåleværdier.
Nevertheless, these model equations should be used with caution, especially when changes in the test substance's bioavailability occur during the test (42).
Institute of Freshwater Ecology
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.
USA
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.
12,750 g
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:
6,082 g
Example of a Sampling Schedule for a 28-day Bioaccumulation Test
2,205 g
Uptake phase (including a 4 d- equilibration phase)
7,350 g
Activities
0,522 g
Preparation of peat suspension for sediment;
7,500 g
conditioning of the suspension for 48 h;
Var(Yi) = σ2/(r0 2 · mi) + ri 2 · σ2/r04 · m0
Spiking of the sediment or sediment fraction;
I sådanne metoder estimeres en empirisk variansfordeling ved hjælp af de målte data sammen med hyppig resampling, der styres af en generator af vilkårlige tal.
mixing of all sediment constituents;
REFERENCER
removing sediment samples of treated and solvent control sediment for determination of test substance concentration;
S. A. L. M. Kooijman, A. O. Hanstveit og N. Nyholm (1996), No-effect concentrations in algal growth inhibition tests, Water Research, 30, 1625-1632.
addition of overlying water;
N. R. Draper og H. Smith (1981), Applied Regression Analysis, second edition, Wiley, New York.
incubation at test conditions (equilibration phase);
R. D. Bruce og D. J. Versteeg (1992), A statistical procedure for modelling continuous toxicity data, Environ.
Separation of the test organisms from the culture for acclimatisation;
Chem.
of water quality (see paragraph 52);
11, 1485-1494.
removing replicates for taking samples of water and sediment for determination of test substance concentration;
J. S. Andersen, H. Holst, H. Spliid, H. Andersen, A. Baun og N. Nyholm (1998), Continuous ecotoxicological data evaluated relative to a control response, Journal of Agricultural, Biological and Environmental Statistics, 3, 405-420.
randomised distribution of the worms to the test chambers;
Celle og tilbehør til måling af koncentrationen af opløst ilt, en passende iltelektrode, en indkapslet celle, som skal indeholde prøven, uden headspace og med en skriver (f.eks. 7, 8, 9 i figur 1 i tillæg 2);
retaining of sufficient sub-samples of worms for determination of analytical background values;
D. Brown, H. R. Hitz og L. Schäfer (1981), The assessment of the possible inhibitory effect of dyestuffs on aerobic waste-water bacteria, Experience with a screening test, Chemosphere 10 (3):
controlling air supply, if closed test system is used;
E. F. King og H. A. Painter (1986), Inhibition of respiration of activated sludge;
Remove replicates for sampling;
variability and reproducibility of results, Toxicity Assessment 1(1):
controlling air supply, worm behaviour, water quality (see paragraph 56);
ISO (2007), ISO 8192 Water Quality — Test for inhibition of oxygen consumption by activated sludge for carbonaceous and ammonium oxidation, Den Internationale Standardiseringsorganisation.
taking water, sediment and worm samples for determination of test substance concentration;
D. J. Bealing (2003), Document ISO/TC147/WGI/N.183, Den Internationale Standardiseringsorganisation.
Controlling air supply, worm behaviour and temperature;
H. A. Painter og K. Jones (1963), The use of the wide-bore dropping-mercury electrode for the determination of the rates of oxygen uptake and oxidation of ammonia by micro-orgranisms, Journal of Applied Bacteriology 26 (3):
Same as day 1;
H. A. Painter (1986), Testing the toxicity of chemicals by the inhibition of respiration of activated sludge, Toxicity Assessment 1:515-524.
4 - 6
B. Robra (1976), Wasser/Abwasser 117, 80.
Same as day 2;
S. Fiebig og U. Noack (2004), The use of copper(II)sulphate pentahydrate as reference substance in the activated sludge respiration inhibition test — acc. to the OECD guideline 209, Fresenius Environmental Bulletin 13 No. 12b:
compensate evaporated water if necessary;