natgillin/translations-raw huggingface dataset:
Report of British Toxicology Society/UK Environmental Mutagen Society Working Group: Dose setting in In vivo Mutagenicity Assays.
G., Morton, D. B., Kirkland, D. J. och Richold, M. (1992), Report of British Toxicology Society/UK Environmental Mutagen Society Working Group: Dose setting in In Vivo Mutagenicity Assays.
Iin: ‘Developments in Science and Practice of Toxicology’, Ed. A.W.
N., and Wehr, C. M. (1983), Micronuclei in Circulating Erythrocytes: A Rapid Screen for Chromosomal Damage During Routine Toxicity Testing in Mice. in: ’Developments in Science and Practice of Toxicology’, ed.
Richold, M., Ashby, J., Bootman, J., Chandley, A., Gatehouse, D.G. and Henderson, L., (1990) In Vivo Cytogenetics Assay. In: D.J.
Richold, M., Ashby, J., Bootman, J., Chandley, A., Gatehouse, D. G. and Henderson, L. (1990), In Vivo Cytogenetics Assay.
Kirkland (Ed.) Basic Mutagenicity tests.
In: D. J. Kirkland (ed) Basic Mutagenicity tests.
UKEMS Recommended Procedures. UKEMS Sub-Committee on Guidelines for Mutagenicity Testing.
UKEMS Recommended Procedures.UKEMS Sub-Committee on Guidelines for Mutagenicity testing.
It is recommended that wherever possible, the use of an aqueous solvent/vehicle be considered first. When testing water-unstable substances, the organic solvents used should be free of water.
Därhelst det är möjligt, rekommenderas att man i första hand överväger vattenbaserade lösningsmedel/vehiklar.
Metabolic activation Cells should be exposed to test chemicals both in the presence and absence of an appropriate exogenous metabolic activation system.
Koncentrationen av vehiklen bör inte orsaka någon ändring av cellers livskraft eller växtegenskaper.
The use of other species, tissues, post-mitochondrial fractions, or procedures may also be appropriate for metabolic activation. Test conditions Tester strains
Cellerna exponeras för testämnet både i närvaro och i frånvaro av ett lämpligt exogent metaboliskt aktiveringssystem.
The most frequently used strains are the diploids D4, D5, D7 and JD1. The use of other strains may be appropriate. Media
Det vanligen använda systemet består av en post-mitokondrial fraktion som kompletterats med en co-faktor, framställd från lever av gnagare som förbehandlats med enzyminducerande medel.
Appropriate positive control chemicals should be used for each specific recombination endpoint. Exposure concentrations
De mest vanligen använda stammarna är de diploida D4, D5, D7 och JD1.
Among the factors to be taken into consideration are cytotoxicity and solubility. The lowest concentration must have no effect on celf viability.
Vid bestämning av överlevnadsgrad och mitotisk rekombination används lämpliga kulturmedier.
Phenotypic expression time: a period during which unaltered gene products are depleted from newly mutated cells. Mutant frequency: the number of mutant cells observed divided by the number of viable cells.
fenotypisk expressionslid: en period under vilken celler som nyligen muterat töms på oförändrade genprodukter. mutantfrekvens: antalet mutanta celler som observerats, delat med antalet livskraftiga celler.
A test substance for which the results do not meet the above criteria is considered non-mutagenic in this test. Although most experiments will give clearly positive or negative results, in rare cases the data set will preclude making a definite judgement about the activity of the test substance.
Även om de flesta experiment kommer att ge tydligt positiva eller negativa resultat, så kan i sällsynta fall uppsättningen av data göra det omöjligt att utföra en otvetydig bedömning med avseende på testsubstansens aktivitet.
In: Genetic Toxicology of Environmental Chemicals, Part B: Genetic Effects and Applied Mutagenesis, Ramel, C., Lambert, B. and Magnusson, J. (Eds.) Liss, New York, p. 477-484.
D., (1986), Clastogenic Potential in Mouse Spermatogonia of Chemical Mutagens Related to their Cell-Cycle Specifications, in: Genetic Toxicology of Environmental Chemicals, Part B: Genetic Effects and Applied Mutagenesis, Ramel, C, Lambert, B. and Magnusson, J. (eds) Liss, New York, s. 477–484.
Lovell, D.P., Anderson, D., Albanese, R., Amphlett, G.E., Clare, G., Ferguson, R., Richold, M., Papworth, D.G. and Savage, J.R.K., (1989) Statistical Analysis of In Vivo Cytogenetic Assays In: D.J. Kirkland (Ed.)
Lovell, D. P., Anderson, D., Albanese, R., Amphlett, G. E., Clarc, G., Ferguson, R., Richold, M., Papworth, D. G. and Savage, J. R. K. (1989), Statistical Analysis of In Vivo Cytogenetic Assays, in: D. J. Kirkland (ed.), Statistical Evaluation of Mutagenicity Test Data.
Statistical Evaluation of Mutagenicity Test Data. UKEMS Sub-Committee on Guidelines for Mutagenicity Testing, report, Part III.
UKEMS Subcommittee on Guidelines for Mutagenicity Testing, report, Part 111.
Route of administration The three main routes of administration are oral, dermal and inhalation.
Det finns tre huvudsakliga tillförselvägar: oral tillförsel, dermal tillförsel respektive tillförsel genom inhalation.
Detailed examination should be made of all preserved organs of all animals of the satellite high-dose and control groups. Where test-substance-related pathology is found in the high-dose satellite group, target organs of all other animals in any other treated satellite group should be subjected to full and detailed histological examination as well as those of the heated groups in the carcinogenicity testing portion of the study at its termination.
En detaljerad undersökning ska göras av alla bevarade organ från alla djur i högdossatellit- och kontrollgrupperna Om det finns patologiska tecken som kan sättas i samband med testämnet i högdossatellitgruppen ska målorganen hos djuren i övriga doserade satellitgrupper samt i de doserade grupperna i den del av undersökningen som gäller cancerogenicitet underkastas en fullständig och detaljerad histologisk undersökning vid försökets avslutning.
Other routes of administration are also acceptable. All animals should be dosed by the same method during the appropriate experimental period.
Andra tillförselvägar är också godtagbara Samma tillförselmetod ska användas för alla djur under hela behandlingsperioden.
Auston and R.V.
Auston och R.V.
Working, P.K. and M. Hurtt, (1987) Computerised Videomicrographic Analysis of Rat Sperm Motility. Journal of Andrology, 8, p. 330-337.
Working, P.K. och M. Hurtt (1987), ”Computerized Videomicrographic Analysis of Rat Sperm Motility”, Journal of Andrology, 8:330–337.
Kang, (1989) Test Methods for Assessing Female Reproductive and Developmental Toxicology. In: Principles and Methods of Toxicology, A.W.
Kang, (1989), ”Test Methods for Assessing Female Reproductive and Developmental Toxicology”, Principles and Methods of Toxicology, A.W.
Thomas, J. A., (1991) Toxic Responses of the Reproductive System. In: Casarett and Doull's Toxicology, M.O.
Thomas, J. A. (1991), ”Toxic Responses of the Reproductive System”, Casarett and Doull's Toxicology, M.O.
Clegg, (1989) Assessment of Male Reproductive Toxicity: A Risk Assessment Approach. In: Principles and Methods of Toxicology, A.W.
Clegg (1989), ”Assessment of Male Reproductive Toxicity: A Risk Assessment Approach”, Principles and Methods of Toxicology, A.W.
This rinsing procedure is then repeated, after which the skin discs are removed and placed into vials containing 5 ml of 30 % (w/v) sodium dodecyl sulphate (SDS) in distilled water and are incubated overnight at 60 oC. After incubation, each skin disc is removed and discarded and the remaining solution is centrifuged for eight minutes at 21 oC (relative centrifugal force ~175 × g). A 1 ml sample of the supernatant is diluted 1 in 5 (v/v) [i.e.
Den kvarvarande lösningen centrifugeras under 8 minuter vid 21 oC (relativ centrifugalkraft cirka 175 x g).
if the mean TER value obtained for the test substance is greater than 5 kΩ; or (ii) the mean TER value is less than or equal to 5 kΩ; and the skin disc is showing no obvious damage, and
om TER-medelvärdet är mindre än eller lika med 5 kΩ och hudbiten är uppenbart skadad eller
if the mean TER value is less than or equal to 5 kΩ and the skin disk is obviously damaged; or (ii) the mean TER value is less than or equal to 5 kΩ; and
hudbiten inte uppvisar någon synlig skada men
the skin disc is showing no obvious damage, but the mean disc dye content is greater than or equal to the mean disc dye content of the 10M HCl positive control obtained concurrently.
medelhalten av färgämne är större än eller lika med medelhalten av färgämne i den parallella positiva kontroll som behandlats med 10 M HCl.
Botham, P.A., Hall, T.J., Dennett, R., McCall, J.C., Basketter, D.A., Whittle, E., Cheeseman, M., Esdaile, D.J., and Gardner, J., (1992) The skin corrosivity test in vitro: results of an interlaboratory trial. Toxic.
Botham, P.A., Hall, T.J., Dennett, R., McCall, J.C., Basketter, D.A., Whittle, E., Cheeseman, M., Esdaile, D.J., and Gardner, J. (1992), The skin corrosivity test in vitro: results of an interlaboratory trial.
The most frequently used assay is MTT (3-(4,5-Dimethylthiazol-2yl)-2,5-diphenyltetrazolium bromide, Thiazolyl blue: EINECS number 206-069-5, CAS number 298-93-1)) reduction, which has been shown to give accurate and reproducible results (5) but others may be used. The skin sample is placed in an MTT solution of appropriate concentration (e.g. 0,3-1 mg/mL) at appropriate incubation temperature for three hours.
Den oftast använda bestämningsmetoden är MTT-reduktion [3-(4,5-dimetylthiazol-2yl)-2,5-difenyltetrazoliumbromid; EINECS-nummer 206-069-5, CAS-nummer 298-93-1)] , som har visat sig ge exakta och reproducerbara resultat (5), men även andra metoder kan användas (t.ex. 0,3-1 mg/ml) vid en lämplig inkubationstemperatur under 3 timmar.
if the viability after three minutes exposure is less than 50 %; or (ii) if the viability after three minutes exposure is greater than or equal to 50 % and the viability after 1 hour exposure is less than 15 %. The test substance is considered to be non-corrosive to skin: (i) if the viability after three minutes exposure is greater than or equal to 50 % and the viability after 1 hour exposure is greater than or equal to 15 %.
om viabiliteten efter 3 minuters exponering är större än eller lika med 50 % och viabiliteten efter 1 timmes exponering är större än eller lika med 15 %.
Ponec, M., Boelsma, E., Weerheim, A., Mulder, A., Boutwstra, J., and Mommaas, M., 2000. Lipid and ultrastructural characterisation of reconstructed skin models. International Journal of Pharmaceutics.
Ponec, M., Boelsma, E., Weerheim, A., Mulder, A., Boutwstra, J., and Mommaas, M., (2000), Lipid and ultrastructural characterization of reconstructed skin models.
It has been suggested that if the molar extinction/absorption coefficient is less than 10 litre × mol-1 × cm-1 the chemical is unlikely to be photoreactive. Such chemical may not need to be tested in the in vitro 3T3 NRU phototoxicity test or any other biological test for adverse photochemical effects (1)(5). See also Appendix 1.
Om den molära extinktions- eller absorptionskoefficienten ligger under 10 liter × mol--1 × cm-1 har kemikalien troligen ingen fotoreaktiv potential och behöver sannolikt inte testas med 3T3 NRU-fototoxicitetstest in vitro eller annat biologiskt test av skadliga fotokemiska effekter (1)(5) (bilaga 1).
(+Irr)
(+UVA)
OECD Giudance Document on Neurotoxicity Testing Strategies and Test Methods. OECD, Paris, In Preparation.
”OECD Giudance Document on Neurotoxicity Testing Strategies and Test Methods”, OECD, Paris (under beredning).
Eds.
P.S.
Williams and Wilkins, Baltimore/London.
Schaumburg, Williams and Wilkins, Baltimore/London.
Gad, S.C., (1982) A Neuromuscular Screen for Use in Industrial Toxicology. J. Toxicol.
Gad (1982), ”A Neuromuscular Screen for Use in Industrial Toxicology”, J. Toxicol.
Broxup, B., (1991) Neuopathology as a screen for Neurotoxicity Assessment. J. Amer.
Broxup (1991), ”Neuropathology as a screen for Neurotoxicity Assessment”, J. Amer.
O'Callaghan, J.P. (1988). Neurotypic and Gliotypic Proteins as Biochemical Markers of Neurotoxicity. Eurotoxicol.
O'Callaghan (1988), ”Neurotypic and Gliotypic Proteins as Biochemical Markers of Neurotoxicity”, Eurotoxicol.
D.A., Lowndes, H.E. and Birkamper, G.G., (1982) Electrophysiological Techniques in Neurotoxicology. In: Nervous System Toxicology.
Birkamper (1982), ”Electrophysiological Techniques in Neurotoxicology”, Nervous System Toxicology, red.
Mitchell, C.L. ed. Raven Press, New York, p. 299-335.
Mitchell, Raven Press, New York, 299–335.
Bancroft, J.D. and Steven A., (1990) Theory and Pratice of Histological Techniques. Chapter 17, Neuropathological Techniques.
Bancroft och A. Steven (1990), ”Theory and Pratice of Histological Techniques, Chapter 17”, Neuropathological Techniques, red.
Lowe, James and Cox, Gordon eds. Churchill Livingstone.
Lowe, James och Cox, Gordon, Churchill Livingstone.
Part 3: Flow-through method.
Del 3: Flow-through method.
Environmental Protection Agency, Methods for the acute toxicity tests with fish, macroinvertebrates and amphibians. The Committee on Methods for Toxicity Tests with Aquatic Organisms, Ecological Research Series EPA-660-75-009, 1975.
Environmental Protection Agency, Methods for the acute toxicity tests with fish, macroinvertebrates and amphibians, The committee on Methods for Toxicity Tests with Aquatic Organisms, Ecological Research Series EPA-660-75-009, 1975.
Commission of the European Communities, Inter-laboratory test programme concerning the study of the ecotoxicityof a chemical substance with respect to the fish. EEC Study D.8368, 22 March 1979.
Commission of the European Communities, Inter-laboratory test programme concerning the study of the ecotoxicity of a chemical substance with respect to the fish, EEC Study D.8368, 22 March 1979.
QUALITY CRITERIA For a test to be valid, the following performance criteria apply:
För att ett försök ska vara giltigt gäller följande kriterier för prestanda:
Stock solutions of mineral components To make up the test solutions, stock solutions of appropriate concentrations of mineral components are made up.
Stamlösningar av oorganiska medier
The dilution factors and, for the MITI test, the specific preparation of the mineral medium are given under the headings of the specific tests. Stock solutions:
Följande stamlösningar kan (med olika förtunningsförhållanden) användas för DOC-eliminering, modifierad OECD-screening, CO2-utveckling, manometrisk respirometri och Closed Bottle-test.
Dissolve in water and make up to 1 litre. Note: in order to avoid having to prepare this solution immediately before use add one drop of conc. HCL or 0,4 g ethylenediaminetetra-acetic acid disodium salt (EDTA) par litre.
Kommentar: För att undvika att behöva framställa denna lösning omedelbart före användning tillsätts 1 droppe koncentrerat HC1 eller 0,40 g etylendiaminotetraättiksyra (EDTA) per liter.
Settle or centrifuge the re-suspended sludge after thorough mixing, discard the supernatant and again re-suspend the washed sludge in a further volume of mineral medium. Repeat this procedure until the sludge is considered to be free from excess substrate or inhibitor.
Utfäll eller centrifugera det omsuspenderade slammet efter noggrann blandning, avlägsna supernatanten och slamma återigen upp det tvättade slammet i en ytterligare mängd oorganiskt medium.
× mg test chemical added
× mg tillsatt testkemikalie
For sodium hydroxide absorbers, calculate the amount of carbon dioxide prodllced, expressed as IC (mg), by multiplying the concentration of IC in the absorbent by the volume of the absorbent. Calculate the percentage degradation from: % of ThCO2
Om natriumhydroxid används som absorptionsmedel beräknas den utvecklade CO2-mängden, uttryckt som IC (mg), genom att multiplicera absorbtionsmedlets IC-koncentration med dess volym.
Surfactants and other soluble organic compounds are removed from the filters by boiling them in deionised water for three periods each of one hour. The filters may then be stored in water for one week.
De ytaktiva ämnena och andra upplösliga organiska ämnen avlägsnas från filtren genom kokning i avjoniserat vatten i tre gånger 1 timme.
SETAC, (1995) Procedures for Assessing the Environmental Fate and Ecotoxicity of Pesticides. Mark R. Lynch, Ed.
SETAC (1995), Procedures for Assessing the Environmental Fate and Ecotoxicity of Pesticides, Mark R. Lynch, Ed.
When the data are adequate the LC50 value and the confidence limits (p = 0,05) should be determined using standard methods (Litchfield and Wilcoxon, 1949, for equivalent method). The LC50 should be given as mg of test substance per kilogram of the test substrate (dry weight).
När erhållna data inte är tillräckliga kan LC50 och dess konfidensgränser (p = 0,05) bestämmas genom användning av standardmetoder (Lichtfield and Wilcoxon, 1949, eller motsvarande metod).
The substances to be studied are used in concentrations corresponding to DOC-values in the range of 50 to 400 mg/litre or COD-values in the range of 100 to 1000 mg/litre (DOC = dissolved organic carbon; COD = chemical oxygen demand). These relatively high concentrations have the advantage of analytical reliability.
De ämnen som ska undersökas används i koncentrationer motsvarande DOC-värden av 50–400 mg/l (DOC = dissolved organic carbon, dvs. upplöst organiskt kol), eller COD-värden motsvarande 100–1000 mg/l (COD = chemical oxygen demand, dvs. kemiskt syrebehov).
The ratio of eliminated DOC (or COD) after each interval to the value three hours after the start is expressed as percentage biodegradation and serves as the measure of the extent of degradation at this time. The result is plotted versus time to give the biodegradation curve.
Förhållandet mellan eliminerat DOC (eller COD) efter varje tidsintervall och värden tre timmar efter testets inledning uttrycks som procentuell bionedbrytning och är ett värde för nedbrytningsgraden vid denna tidpunkt.
Air flow 0,5 to 1 litre/minute Measuring apparatus:
Flatbottnad kolv som t.ex. en BOD-kolv (se figur 1)
Oxygen meter: Suitable oxygen electrode, with a recorder
Syreelektrod med tillhörande skrivare
Percentage biodegradition, Dda
Procent bionedbrytning
Feeding During the acclimation and test periods, fish are fed with an appropriate diet of known lipid and total protein content, in an amount sufficient to keep them in a healthy condition and to maintain body weight.
Utfodring
Final report March 1987. Authors: P. Kristensen and N. Nyholm.
Biokoncentration av kemikalier i fisk: genomflödesmetoden – Ringprovningsprogrammet 1984–1985), slutrapport 1987, författare: P. Kristensen and N. Nyholm.
Technol.
Fördelning av organiska blandningar i oktanol-vattensystem; miljö; forsk ning; teknik).
Ernst W. (1985) Accumulation in Aquatic organisms. In: Appraisal of tests to predict the environmental behaviour of chemicals. Ed. by Sheehman P., Korte F., Klein W. and Bourdeau P.H. Part 4.4 pp 243-255.
Ernst W.
Crossland N.O. (1985) A method to evaluate effects of toxic chemicals on fish growth.
Grossland N. O. (1985), A method to evaluate effects of toxic chemicals on fish growth.
A series of five (or more) successive concentrations may be chosen from a column. Mid-points between concentrations in column (x) are found in column (2x + 1).
En serie av fem (eller flera) på varandra följande koncentrationer kan väljas ur en kolumn, Mittpunkterna mellan koncentrationerna i kolumn (x) finns i kolumn (2x + 1).
Details on holding the brood stock under satisfactory conditions may be found in OECD TG 210 and in references (2)(3)(4)(5)(6).1.6.4. Handling of embryos and larvae
Närmare uppgifter om lämplig förvaring av fiskyngelstammen finns i OECD TG 210 och i hänvisningarna (2), (3), (4), (5), (6).1.6.4 Hantering av embryon och yngel
Hisaoka K.K. and Battle H.I., (1958). The Normal Development Stages of the Zebrafish Brachydanio rerio (Hamilton-Buchanan) J. Morph., 102, p. 311.
Hisaoka K. K. and Battle H. I. (1958), The Normal Development Stages of the Zebrafish Brachydanio rerio (Hamilton-Buchanan) J. Morph., 102, 311 sidor.
Nagel R., (1986). Untersuchungen zur Eiproduktion beim Zebrabärbling (Brachydanio rerio Hamilton-Buchanan).
Nagel R. (1986), Untersuchungen zur Elproduktion beim Zebrabärbling (Brachydanio rerio Hamilton-Buchanan).
Finney D.J., (1971). Probit Analysis, 3rd ed., Cambridge University Press, Great Britain, p. 1-333.
Finney D. J. (1971), Probit Analysis, 3rd cd., Cambridge University Press, Great Britain, s. 1–333.
Stephan C.E., (1982). Increasing the Usefulness of Acute Toxicity Tests.
Stephan C. E. (1982), Increasing the Usefulness of Acute Toxicity Tests.
Foster and W.E. Bishop, Eds., American Society for Testing and Materials, p. 69-81.
Bishop, Eds., American Society for Testing and Materials, s. 69–81.
Williams D.A., (1971). A Test for Differences Between Treatment Means when Several Dose Levels are Compared with a Zero Dose Control.
Williams D. A. (1971), A Test for Differences Between Treatment Means when Several Dose Levels are Compared with a Zero Dose Control.
Williams D.A., (1972). The Comparison of Several Dose Levels with a Zero Dose Control.
Williams D. A. (1972), The Comparison of Several Dose Levels with a Zero Dose Control.
Sokal R.R. and Rohlf F.J., (1981). Biometry, the Principles and Practice of Statistics in Biological Research, W.H.
Sokal R. R. and Rohlf F. J. (1981), Biometry, the Principles and Practice of Statistics in Biological Research, W.
EPPO bulletin, vol. 23, N.1, 151-165. March 1993.
EPPO Bulletin, Vol. 23, N.l. s. 151–165, March 1993.
EPPO/Council of Europe (1993) Decision-Making Scheme for the Environmental Risk Assessment of Plant Protection Products — Honeybees. EPPO bulletin, vol. 23, N.1, p. 151-165.
EPPO/Council of Europe (1993), Decision-Making Scheme for the Environmental Risk Assessment of Plant Protection Products – Honeybees, EPPO bulletin, Vol. 23, N.l, s. 151–165.
Gough, H. J., McIndoe, E.C., Lewis, G.B., (1994) The use of dimethoate as a reference compound in laboratory acute toxicity tests on honeybees (Apis mellifera L.), 1981-1992. Journal of Apicultural Research 22, p. 119-125.
Gough, H. J., McIndoe, E. C, Lewis, G. B. (1994), The use of dimethoate as a reference compound in laboratory acute toxicity tests on honeybees (Apis mellifera L.), 1981–1992, Journal of Apicultural Research 22, s. 119–125.
Litchfield, J.T. and Wilcoxon, F., (1949) A simplified method of evaluating dose-effect experiments. Jour.
Litchfield, J. T. and Wilcoxon, F. (1949), A simplified method of evaluating dose-effect experiments, Jour.
In the preliminary study, samples may be collected sequentially over a 48 h period of mixing (for example at 4, 8, 24, 48 h). However, times of analysis should be considered with flexibility with respect to the work schedule of the laboratory.
Vid den förberedande undersökningen kan sekventiella prover tas under en omröringstid på 48 timmar, t.ex. vid 4, 8, 24 och 48 timmar, men analystidpunkterna kan också anpassas till arbetsschemat på laboratoriet.
Common plots of the percentage desorption Dti and adsorption Ati
Adsorptionsprocessens reversibilitet kan uppskattas med hjälp av ett diagram där den procentuella desorptionen Dti
, elsewhere denoted as x/m) is calculated. It is assumed that equilibrium has been attained and that Cs
, på andra ställen betecknat som x/m) beräknas för varje provrör, under antagandet att jämvikt har inträtt och attCs
and 1/n are calculated by regression analysis using the equation 9. The correlation coefficient r2 of the log equation is also calculated.
och l/n beräknas med regressionsanalys med hjälp av ekvation 9.
Kuhnt G. and Muntau H. (Eds.) EURO-Soils: Identification, Collection, Treatment, Characterisation.
Kuhnt G. and Muntau H. (Eds.), EURO-Soils: Identification, Collection, Treatment, Characterisation.
Lambert S.M., Porter P.E., and Schieferrstein R.H., (1965) ‘Movement and sorption of chemicals applied to the soil’. Weeds, 13, p. 185-190.
Lambert S. M., Porter P. E. and Schieferrstein R. H. (1965), ”Movement and sorption of chemicals applied to the soil”, Weeds, 13, s. 185–190.
Hance R.J., (1969) ‘An empirical relationship between chemical structure and the sorption of some herbicides by soils’. J. Agri.
Hance R. J.(1969), ”An empirical relationship between chemical structure and the sorption of some herbicides by soils”, Agri.