natgillin/translations-raw huggingface dataset:
Convert depuration phase tissue concentrations (mass of test substance/unit mass of fish) into mass of test substance/fish: match concentrations and individual fish weights in tabular form (e.g. using a computer spreadsheet) and multiply each concentration by the total fish weight for that measurement to give a set of mass test substance/fish for all depuration phase samples.
Koncentracije opažene u tkivima tijekom faze izlučivanja (masa ispitivane tvari/jedinična masa ribe) preračunavaju se u masu ispitivane tvari po ribi: koncentracije i pojedinačne mase riba povezuju se u obliku tablice (npr. primjenom računalne tablice) te se svaka koncentracija množi s masom cijele ribe kako bi se dobio skup podataka ‚masa ispitivane tvari/riba’ za sve uzorke faze izlučivanja.
Plot the resulting natural logarithm of substance mass data against time for the experiment (depuration phase) as would be done normally.
Prirodni logaritam dobiven iz podataka o masi tvari grafički se prikazuje u odnosu na vrijeme izvođenja pokusa (faza izlučivanja), kao i inače.
For the aqueous exposure method, derive the uptake rate constant routinely (see sections 4 and 6) note that the “normal” k2 value should be used in the curve fitting equations for k1) and derive the depuration rate constant from the above data.
Za metodu vodenog izlaganja, konstanta brzine apsorpcije izračunava se na uobičajen način (vidjeti odjeljke 4. i 6.; treba napomenuti da bi u jednadžbama za prilagođavanje krivulje za k1 trebalo upotrijebiti ‚normalnu’ vrijednost k2) te se iz prethodno navedenih podataka izvodi konstanta brzine izlučivanja.
Because the resulting value for the depuration rate constant is independent of growth as it has been derived on a mass basis per whole fish, it should be denoted as k2g and not k2.
Budući da vrijednost dobivena za konstantu brzine izlučivanja ne ovisi o rastu jer je izračunata na osnovi mase po cijeloj ribi, trebalo bi je označiti kao k2g, a ne kao k2.
LIPID NORMALISATION TO 5 % LIPID CONTENT (AQUEOUS EXPOSURE METHOD ONLY)
NORMIRANJE LIPIDA NA SADRŽAJ LIPIDA OD 5 % (JEDINO METODA VODENOG IZLAGANJA)
BCF results (kinetic and steady-state) from aqueous exposure tests should also be reported relative to a default fish lipid content of 5 % wet weight, unless it can be argued that the test substance does not primarily accumulate in lipid (e.g. some perfluorinated substances may bind to proteins).
O rezultatima za BCF (kinetički i u stabilnom stanju) dobivenima ispitivanjima u kojima je primijenjeno vodeno izlaganje trebalo bi izvijestiti i u odnosu na zadani sadržaj lipida u ribi od 5 % mokre mase, osim ako se može dokazati da se ispitivana tvar ne akumulira ponajprije u lipidima (npr. neke se perfluorirane tvari mogu vezati na proteine).
Fish concentration data, or the BCF, need to be converted to a 5 % lipid content wet weight basis.
Koncentracije u ribama ili vrijednost BCF potrebno je preračunati u sadržaj lipida od 5 % u odnosu na mokru masu.
If the same fish were used for measuring substance concentrations and lipid contents at all sampling points, this requires each individual measured concentration in the fish to be corrected for that fish's lipid content.
Ako su u svim točkama uzorkovanja upotrijebljene iste ribe za mjerenje koncentracija tvari i sadržaja lipida, svaku pojedinačnu koncentraciju izmjerenu u ribi potrebno je ispraviti u odnosu na sadržaj lipida u toj ribi.
Arnot J.A. and Gobas F.A.P.C.
Arnot J.A. and Gobas F.A.P.C.
Kristensen P. (1991), Bioconcentration in fish: comparison of BCF's derived from OECD and ASTM testing methods; influence of particulate matter to the bioavailability of chemicals.
Kristensen P. (1991), Bioconcentration in fish: comparison of BCF's derived from OECD and ASTM testing methods; influence of particulate matter to the bioavailability of chemicals.
Konemann H. and van Leeuwen K. (1980), Toxicokinetics in fish: Accumulation and elimination of six chlorobenzenes by guppies.
Konemann H. and van Leeuwen K. (1980), Toxicokinetics in fish: Accumulation and elimination of six chlorobenzenes by guppies.
CALCULATION OF ASSIMILATION EFFICIENCY AND BIOMAGNIFICATION FACTOR
IZRAČUNAVANJE UČINKOVITOSTI ASIMILACIJE I FAKTORA BIOMAGNIFIKACIJE
To calculate the assimilation efficiency, the overall depuration rate constant should first be estimated according to section 4 of Appendix 5 (using the “sequential method”, i.e. standard linear regression) using mean sample concentrations from the depuration phase.
Da bi se izračunala učinkovitost asimilacije, prvo je potrebno procijeniti ukupnu konstantu brzine izlučivanja u skladu s odjeljkom 4. Dodatka 5. (s pomoću ‚sekvencijske metode’, tj. standardne linearne regresije) na temelju srednjih vrijednosti koncentracija izmjerenih u uzorcima tijekom faze izlučivanja.
The feeding rate constant, I, and uptake duration, t, are known parameters of the study.
Konstanta brzine hranjenja, I, i trajanje apsorpcije, t, poznati su parametri ispitivanja.
Cfood, the mean measured concentration of the test substance in the food is a measured variable in the study.
Cfood, srednja izmjerena koncentracija ispitivane tvari u hrani, varijabla je koja se mjeri tijekom ispitivanja.
C0,d, the test substance concentration in the fish at the end of the uptake phase, is usually derived from the intercept of a plot of ln(concentration) vs. depuration day.
C0,d, koncentracija ispitivane tvari u ribi na kraju faze apsorpcije, obično se izvodi iz odsječka pravca koji prikazuje ln(koncentracija) u ovisnosti o danu izlučivanja.
The substance assimilation efficiency (a, absorption of test substance across the gut) is calculated as:
Učinkovitost asimilacije tvari (a, apsorpcija ispitivane tvari u cijeloj utrobi) izračunava se kao:
[Equation A7.1]
[jednadžba A7.1]
derived concentration in fish at time zero of the depuration phase (mg kg– 1);
izvedena koncentracija u ribi u nultom vremenu faze izlučivanja (mg kg– 1);
concentration in food (mg kg– 1 food);
koncentracija u hrani (mg kg– 1 hrane);
[Equation A7.2]
[jednadžba A7.2]
mean fish weight at uptake day t
srednja masa ribe na dan t faze apsorpcije
mean fish weight at the start of the experiment
srednja masa ribe na početku pokusa
In this way (at least) the mean fish weight on the last day of exposure (Wf,end-of-uptake) can be estimated.
Na ovaj se način (u najmanju ruku) može procijeniti srednja masa ribe zadnjeg dana izlaganja (Wf,end-of-uptake).
As the feeding rate was set based on Wf,0, the effective feeding rate for each day of uptake can be calculated using these two weight values.
S obzirom na to da je brzina hranjenja utvrđena na temelju Wf,0, stvarna brzina hranjenja za svaki dan faze apsorpcije može se izračunati primjenom tih dviju masenih vrijednosti.
The growth-corrected feeding rate, Ig (g food g-1 fish day– 1), to use instead of I in cases of rapid growth during the uptake phase, can then be calculated as
Brzina hranjenja ispravljena u odnosu na rast, Ig (g hrane g– 1 ribe dan– 1), koju treba upotrijebiti umjesto I u slučaju brzog rasta tijekom faze apsorpcije, može se tada izračunati kao:
Sijm D.T.H.M., Pärt P. and Opperhuizen A. (1993), The influence of temperature on the uptake rate constants of hydrophobic compounds determined by the isolated perfused gills of rainbow trout (Oncorhynchus mykiss).
Sijm D.T.H.M., Pärt P. and Opperhuizen A. (1993), The influence of temperature on the uptake rate constants of hydrophobic compounds determined by the isolated perfused gills of rainbow trout (Oncorhynchus mykiss).
Sijm D.T.H.M., Verberne M.E., Part P. and Opperhuizen A. (1994), Experimentally determined blood and water flow limitations for uptake of hydrophobic compounds using perfused gills of rainbow trout (Oncorhynchus mykiss): Allometric applications.
Sijm D.T.H.M., Verberne M.E., Part P. and Opperhuizen A. (1994), Experimentally determined blood and water flow limitations for uptake of hydrophobic compounds using perfused gills of rainbow trout (Oncorhynchus mykiss): Allometric applications.
Barber M.C.
Barber M.C.
Opperhuizen A. (1986), Bioconcentration of hydrophobic chemicals in fish, in Aquatic Toxicology and Environmental Fate, STP 921, Poston, T.M. and Purdy, R., Editors.
Opperhuizen A. (1986), Bioconcentration of hydrophobic chemicals in fish, in Aquatic Toxicology and Environmental Fate, STP 921, Poston, T.M. and Purdy, R., Editors.
Campfens J. and Mackay D. (1997), Fugacity-based model of PCB bioaccumulation in complex aquatic food webs.
Campfens J. and Mackay D. (1997), Fugacity-based model of PCB bioaccumulation in complex aquatic food webs.
Crookes M. and Brooke D. (2010), Estimation of fish bioconcentration factor (BCF) from depuration data.
Crookes M. and Brooke D. (2010), Estimation of fish bioconcentration factor (BCF) from depuration data.
Gobas F. and Morrison H. (2000), Bioconcentration and biomagnification in the aquatic environment, in Handbook of property estimation methods for chemicals, Boethling, R.S. and Mackay, D., Editors.
Gobas F. and Morrison H. (2000), Bioconcentration and biomagnification in the aquatic environment, in Handbook of property estimation methods for chemicals, Boethling, R.S. and Mackay, D., Editors.
95 % confidence intervals are calculated for individual treatment means.
Intervali pouzdanosti od 95 % izračunavaju se za pojedinačne srednje izmjerene vrijednosti tretiranja.
The number of surviving parents in the untreated controls is a validity criterion, and should be documented and reported.
Broj preživjelih roditeljskih životinja u netretiranim kontrolama kriterij je valjanosti i trebalo bi ga zabilježiti i dokumentirati.
Also all other detrimental effects, e.g. abnormal behavior and toxicological significant findings, should be reported in the final report as well.
Jednako tako, u završnom izvješću trebalo bi dokumentirati sve ostale štetne učinke, npr. neuobičajeno ponašanje i toksikološki značajne nalaze.
ECx-values, including their associated lower and upper confidence limits, are calculated using appropriate statistical methods (e.g. logistic or Weibull function, trimmed Spearman-Karber method, or simple interpolation).
Vrijednosti ECx, uključujući s njima povezane donje i gornje granice pouzdanosti, izračunavaju se prikladnim statističkim metodama (npr. logističkom ili Weibullovom funkcijom, modificiranom Spearman-Karberovom metodom ili jednostavnom interpolacijom).
To compute the EC10, EC50 or any other ECx, the complete data set should be subjected to regression analysis.
Za izračun EC10, EC50 ili bilo koje drugog ECx trebalo bi cjelokupan skup podataka podvrgnuti regresijskoj analizi.
If a statistical analysis is intended to determine the NOEC/LOEC appropriate statistical methods should be used according to OECD Document 54 on the Current Approaches in the Statistical Analysis of Ecotoxicity Data: a Guidance to Application (4).
Ako je cilj statističke analize utvrditi NOEC/LOEC, trebalo bi primijeniti prikladne statističke metode u skladu s Dokumentom OECD-a 54 o postojećim pristupima statističkoj analizi podataka o ekotoksičnosti: Smjernice za primjenu (4.).
In general, adverse effects of the test chemical compared to the control are investigated using one-tailed hypothesis testing at p ≤ 0,05.
Općenito, štetni učinci ispitivane kemikalije u usporedbi s kontrolom istražuju se primjenom jednosmjernog ispitivanja hipoteze pri p ≤ 0,05.
the nominal test concentrations and the results of all analyses to determine the concentration of the test chemical in the test vessels (see example data sheets in Appendix 5); the recovery efficiency of the method and the limit of determination should also be reported;
nazivne ispitne koncentracije i rezultati svih analiza za utvrđivanje koncentracije ispitivane kemikalije u ispitnim posudama (vidjeti primjer obrazaca za dostavu podataka u Dodatku 5.), trebalo bi dokumentirati i učinkovitost izdvajanja za metodu te granicu utvrđivanja,
water quality within the test vessels (i.e. pH, temperature and dissolved oxygen concentration, and TOC and/or COD and hardness where applicable) (see example data sheet in Appendix 4);
kakvoća vode u ispitnim posudama (odnosno pH-vrijednost, temperatura i koncentracija otopljenog kisika, TOC i/ili KPK i tvrdoća ako je to primjenjivo) (vidjeti primjer obrasca za dostavu podataka u Dodatku 4.),
OECD Test Guidelines Programme.
OECD Test Guidelines Programme.
OECD (1997).
OECD (1997).
OECD (2006).
OECD (2006). Current Approaches in the Statistical Analysis of Ecotoxicity Data: A Guidance to Application, OECD Environment, Health and Safety Publications (EHS), Series on Testing and Assessment, No.
Baird, D.J., et al.
Baird, D.J., et al. (1991).
Elendt, B.-P.
Elendt, B.-P.
EPA (2002).
EPA (2002).
Vigano, L. (1991).
Vigano, L. (1991).
ASTM.
ASTM.
In: Annual Book of ASTM Standards; Water and Environmental Technology, vol. 11.04; ASTM E729 — 96 (2007) American Society for Testing and Materials, Philadelphia, PA
U: Annual Book of ASTM Standards; Water and Environmental Technology, vol. 11.04; ASTM E729 – 96 (2007) American Society for Testing and Materials, Philadelphia, PA.
In: Proceedings of the 1st European Conference on Ecotoxicology.
U: Proceedings of the 1st European Conference on Ecotoxicology.
(H. Løkke, H. Tyle and F. Bro-Rasmussen. Eds.) pp 144-148.
(H. Løkke, H. Tyle and F. Bro-Rasmussen. Eds.) str. 144. – 148.
Parkhurst, B.R., J.L Forte.
Parkhurst, B.R., J.L Forte.
Cowgill, U.M. and Milazzo, D.P.
Cowgill, U.M. and Milazzo, D.P.
Sims, I.R., S. Watson. and D. Holmes (1993) Toward a standard Daphnia juvenile production test.
Sims, I.R., S. Watson. and D. Holmes (1993) Toward a standard Daphnia juvenile production test.
Sims, I. (1993).
Sims, I. (1993).
Mc Graw Hill Series in Population Biology, New York, p 532.
Mc Graw Hill Series in Population Biology, New York, str. 532.
N.B:
N.B.
Temp (°C) [1]
Temperatura (°C) [1]
Brauhn, J.L. and R.A.
Brauhn, J.L. and R.A.
Brungs, W.A. and B.R.
Brungs, W.A. and B.R.
Hansen, D.J. and P.R.
Hansen, D.J. and P.R.
Gonzalez-Doncel, M. et al (2005), A quick reference guide to the normal development of Oryzias latipes (Teleostei, Adrinichthydae) Journal of Applied Ichthyology, 20:1–14.
Gonzalez-Doncel, M. et al. (2005), A quick reference guide to the normal development of Oryzias latipes (Teleostei, Adrinichthydae) Journal of Applied Ichthyology, 20:1–14.
Devlin, E.W. et al. (1996), Prehatching Development of the Fathead Minnow, Pimephales promelas Rafinesque.
Devlin, E.W. et al. (1996), Prehatching Development of the Fathead Minnow, Pimephales promelas Rafinesque.
Rao, J.N.K. and A.J.
Rao, J.N.K. and A.J.
Rand, G.M. and S.R.
Rand, G.M. and S.R.
15-35 [5]
15 – 35 [5]
A simple method for the analysis of clustered binary data, Biometrics 48, 577-585.
A simple method for the analysis of clustered binary data, Biometrics 48, 577-585.
A simple method for analyzing overdispersion in clustered Poisson data, Statistics in Medicine 18, 1373-1385.
A simple method for analyzing overdispersion in clustered Poisson data, Statistics in Medicine 18, 1373-1385.
Flow chart for ECx Estimation of Replicate Mean Length, Weight, or Proportion of Egg Hatch or Larval Mortality, see text for more details
Dijagram toka za procjenu vrijednosti ECx za srednju vrijednost dužine, težine ili udjela valjenja iz jajašaca ili smrtnosti ličinaka u ponovljenom uzorku; vidjeti tekst za više podataka.
Bruce-Versteeg
Bruce-Versteegov model,
Michaelis-Menten
Michaelis-Menten,
Hill
Hillov model.
Each ELISA plate used for VTG assays should include the following quality control samples: at least 6 calibration standards covering the range of expected VTG concentrations, and at least one non-specific binding assay blank (analysed in duplicate).
Na svakoj pločici ELISA za testove VTG-a trebali bi se nalaziti sljedeći uzorci za kontrolu kvalitete: najmanje šest kalibracijskih standarda kojima je obuhvaćen raspon očekivanih koncentracija VTG-a i najmanje jedna nespecifična, obvezujuća slijepa proba (analiziraju se dva ponavljanja).
Absorbance of these blanks should be less than 5 % of the maximum calibration standard absorbance.
Apsorbancija u tim slijepim probama trebala bi biti manja od 5 % maksimalne apsorbancije pri standardnoj kalibraciji.
OECD Environmental Health and Safety Publications Series on Testing and Assessment No.94, Paris.
94, Pariz.
Androgenic and estrogenic effects of the synthetic androgen 17alpha-methyltestosterone on sexual development and reproductive performance in the fathead minnow (Pimephales promelas) determined using the gonadal recrudescence assay.
Androgenic and estrogenic effects of the synthetic androgen 17alpha-methyltestosterone on sexual development and reproductive performance in the fathead minnow (Pimephales promelas) determined using the gonadal recrudescence assay.
Seki M, et al (2004).
Seki M, et al. (2004).
VTG
VTG,
Photoperiod (dawn / dusk transitions are optional, however not considered necessary)
Fotoperiod (postupno pojačavanje svjetla u zoru odnosno smanjivanje u sumrak moguće je, no ne smatra se nužnim)
16 h light, 8 h dark
16 sati svjetla, 8 sati tame
Homogenisation buffer:(50 mM Tris-HCl pH 7,4; 1 % Protease inhibitor cocktail (Sigma)): 12 ml Tris-HCl pH 7,4 + 120 μl Protease inhibitor cocktail.TRIS: TRIS-ULTRA PURE (ICN) e.g. from Bie & Berntsen, Denmark.Protease inhibitor cocktail: From Sigma (for mammalian tissue) Product number P 8340.NOTE: The homogenisation buffer should be used the same day as manufactured.
Pufer za homogenizaciju:(50 mM Tris-HCl pH 7,4; 1-postotni koktel inhibitora proteaze (Sigma)): 12 ml Tris-HCl pH 7,4 + 120 μl koktela inhibitora proteaze.TRIS: TRIS-ULTRA PURE (ICN), primjerice proizvođača Bie & Berntsen, Danska.Koktel inhibitora proteaze: proizvođača Sigma (za tkivo sisavaca), broj proizvoda P 8340.NAPOMENA: Pufer za homogenizaciju treba upotrijebiti na dan proizvodnje.
ISO (2007) International Standard Water quality — Determination of the acute toxicity of waste water to zebrafish eggs (Danio rerio).
ISO (2007) International Standard Water quality – Determination of the acute toxicity of waste water to zebrafish eggs (Danio rerio).
Schulte, C. and Nagel, R. (1994) Testing acute toxicity in embryo of zebrafish, Brachydanio rerio as alternative to the acute fish test — preliminary results.
Schulte, C. and Nagel, R. (1994) Testing acute toxicity in embryo of zebrafish, Brachydanio rerio as alternative to the acute fish test – preliminary results.
Lange, M., Gebauer, W., Markl, J. and Nagel, R. (1995) Comparison of testing acute toxicity on embryo of zebrafish (Brachydanio rerio), and RTG-2 cytotoxicity as possible alternatives to the acute fish test.
Lange, M., Gebauer, W., Markl, J. and Nagel, R. (1995) Comparison of testing acute toxicity on embryo of zebrafish (Brachydanio rerio), and RTG-2 cytotoxicity as possible alternatives to the acute fish test.
Kammann, U., Vobach, M. and Wosniok, W.
Kammann, U., Vobach, M. and Wosniok, W.
Groth, G., Kronauer, K. and Freundt, K.J.
Groth, G., Kronauer, K. and Freundt, K.J.
Groth, G., Schreeb, K., Herdt, V. and Freundt, K.J.
Groth, G., Schreeb, K., Herdt, V. and Freundt, K.J.
Nguyen, L.T. and Janssen, C.R.
Nguyen, L.T. and Janssen, C.R.
Cheng, S.H., Wai, A.W.K., So, C.H. and Wu, R.S.S.
Cheng, S.H., Wai, A.W.K., So, C.H. and Wu, R.S.S.
Water quality — Determination of the acute lethal toxicity of substances to a freshwater fish [Brachydanio rerio Hamilton-Buchanan (Teleostei, Cyprinidae)].
Water quality – Determination of the acute lethal toxicity of substances to a freshwater fish [Brachydanio rerio Hamilton-Buchanan (Teleostei, Cyprinidae)].
Kimmel, C.B., Ballard, W.W., Kimmel, S.R., Ullmann, B. and Schilling, T.F.
Kimmel, C.B., Ballard, W.W., Kimmel, S.R., Ullmann, B. and Schilling, T.F.
28: 1970-1978
28: 1970-1978.
Water quality — Guidance on statistical interpretation of ecotoxicity data ISO TS 20281.
Water quality – Guidance on statistical interpretation of ecotoxicity data ISO TS 20281.
Scheme of the zebrafish embryo acute toxicity test procedure (from left to right): production of eggs, collection of the eggs, pre-exposure immediately after fertilisation in glass vessels, selection of fertilised eggs with an inverted microscope or binocular and distribution of fertilised eggs into 24-well plates prepared with the respective test concentrations/controls, n = number of eggs required per test concentration/control (here 20), hpf = hours post-fertilisation.
Nacrt postupka ispitivanja akutne toksičnosti na embrijima zebrica (slijeva nadesno): proizvodnja jajašaca, sakupljanje jajašaca, prethodno izlaganje u staklenim posudama odmah nakon oplodnje, odabir oplođenih jajašaca s pomoću invertnog mikroskopa i/ili binokularnog mikroskopa i raspodjela oplođenih jajašaca u pripremljene ploče s 24 bunarića s odgovarajućim ispitnim koncentracijama / kontrolama; n = broj jajašaca potrebnih po ispitnoj koncentraciji / kontroli (ovdje 20), hpf = sati nakon oplodnje.
Versteeg (1992), A statistical procedure for modelling continuous toxicity data, Environmental Toxicology and Chemistry, Vol. 11/10, pp. 1485-1494.
Versteeg (1992), A statistical procedure for modelling continuous toxicity data, Environmental Toxicology and Chemistry, Vol. 11/10, str. 1485-1494.
Barko (1985), Laboratory culture of submersed freshwater macrophytes on natural sediments, Aquatic Botany, Vol. 21/3, pp. 251-263.
Barko (1985), Laboratory culture of submersed freshwater macrophytes on natural sediments, Aquatic Botany, Vol. 21/3, str. 251-263.
Versteeg (1992), A statistical procedure for modelling continuous toxicity data, Environmental Toxicology and Chemistry, Vol. 11/10, 1485-1494.
Versteeg (1992), A statistical procedure for modelling continuous toxicity data, Environmental Toxicology and Chemistry, Vol. 11/10, 1485-1494.
Brain, P., R. Cousens (1989), An equation to describe dose-responses where there is stimulation of growth at low doses, Weed Research, Vol. 29/2, pp/ 93-96.
Brain, P., R. Cousens (1989), An equation to describe dose-responses where there is stimulation of growth at low doses, Weed Research, Vol. 29/2, str. 93-96.
Details of procedure, precautions, and calculation are given in standard tests, e.g. references (1), (2), (3), (4).
Detaljne pojedinosti o postupku, mjerama opreza i izračunu navedene su u standardnim ispitivanjima, npr. u literaturi 1., 2., 3., 4.
Spectrophotometric method
Spektrofotometrijska metoda
This may be done, either by adding increments of concentrated acid (base) to a relatively large volume of a solution of the substance in a multicomponent buffer, initially at high (low) pH (ref. 5), or by adding equal volumes of a stock solution of the substance in e.g. water, methanol, to constant volumes of various buffer solutions covering the desired pH range.
To se može postići dodavanjem koncentrirane kiseline (baze) u relativno velik volumen otopine tvari u višekomponentnom puferu, počevši pri visokoj (niskoj) pH-vrijednosti (literatura 5.), ili dodavanjem jednakih količina matične otopine tvari, npr. u vodi ili metanolu, u stalne volumene različitih puferskih otopina kojima je obuhvaćen željeni raspon pH-vrijednosti.
From the pH and absorbance values at the chosen wavelength, a sufficient number of values for the pKa is calculated using data from at least 5 pHs where the substance is at least 10 per cent and less than 90 per cent ionised.
Iz pH-vrijednosti i vrijednosti apsorbancije na izabranoj valnoj duljini izračunava se dovoljan broj vrijednosti za pKa, pri čemu se upotrebljavaju podaci dobiveni za najmanje pet pH-vrijednosti pri kojima stupanj ionizacije tvari iznosi najmanje 10 %, a manje od 90 %.
SUPPLEMENT TO TEST METHOD B.5 [5]
DODATAK ISPITNOJ METODI B.5. [5]
A SEQUENTIAL TESTING STRATEGY FOR EYE IRRITATION AND CORROSION
STRATEGIJA SEKVENCIJSKOG ISPITIVANJA NADRAŽIVANJA I NAGRIZANJA OKA
Genotoxicity of a Freshwater Cyanotoxin,Cylindrospermopsin, in Two Human Cell Lines: Caco-2 and HepaRG.
Genotoxicity of a Freshwater Cyanotoxin,Cylindrospermopsin, in Two Human Cell Lines: Caco-2 and HepaRG.