natgillin/translations-raw huggingface dataset:
Data er i det følgende opdateret. 
The following data have been updated.
7.3.4.4 Klassificering og grænseværdier 
7.3.4.4 Classification and threshold values
Stoffet er opført på den vejledende liste til selvklassificering (Miljøministeriet, 2005) og klassificeres som: 
The substance is included in the guiding list for self-classification (Danish Ministry of the Environment, 2005) and is classified as:
Den arbejdshygiejniske grænseværdi for stoffet er 3 mg/m³ (At-vejledning, 2007). 
The working environment threshold value for the substance is 3 mg/m³ (Danish Working Environment Authority (WEA) guide, 2007).
Data er baseret på risikovurderingen for stoffet (Rar dibutylftalat). 
The data are based on the risk assessment for the substance (Rar dibutyl phthalate).
Den akutte toksicitet er meget lav: 
The acute toxicity is very low:
LD50 mus, oral 4.840 mg/kg (Rar dibutylftalat) 
LD50 mouse, oral 4,840 mg/kg (Rar dibutyl phthalate)
LD50 kanin, dermal 20.000 mg/kg (Rar dibutylftalat) 
LD50 rabbit, dermal 20,000 mg/kg (Rar dibutyl phthalate)
Stoffet er ikke konstateret sensibiliserende i test på forsøgsdyr (Rar dibutylftalat). 
The substance has not been found to be sensitising in animal tests (Rar dibutyl phthalate).
Der er findes ifølge (Rar dibutylftalat) ikke data, som kan afgøre, om der er cancerogene effekter for stoffet. 
According to (Rar dibutyl phthalate), there are no data to decide whether the substance has carcinogenic effects.
Maksimumindholdet i væske fra udvaskning er 178 µg dibutylftalat pr. liter væske med 100 gram granulat. 
The maximum content in liquid from leaching is 178 µg dibutyl phthalate per litre of liquid with 100 g of granules.
Ved oral optagelse antages 100 % optagelse. 
For oral intake, 100% uptake is assumed.
Optagelse, oral = 0,093 g/kg * 1 * 1,78 µg/g = 0,16 µg/kg k.v./dag. 
Intake, oral = 0.093 g/kg * 1 * 1.78 µg/g = 0.16 µg/kg of body weight/day.
Stoffet fremkalder leverskader i rotter ved NOAEL = 152 mg/kg/dag og fosterskadende effekter ved LOAEL = 52 mg/kg/dag. 
The substance causes hepatic damage in rats at a NOAEL of 152 mg/kg/day and has teratogenic effects at a LOAEL of 52 mg/kg/day.
Ud fra LOAEL for rotter på ca. 52 mg/kg/dag fås en sikkerhedsmargin på MOS = 52/0,00016 = 314.000 ved oralt optag. 
A LOAEL for rats of 52 mg/kg/day gives a safety margin of MOS = 52/0.00016 = 314,000 for oral intake.
Drænvandet kan sive ned gennem den underliggende jord med mulig forurening af grundvandet til følge. 
The drainage water can seep through the underlying soil and potentially contaminate the groundwater.
Drænvandet kan afledes via kloak med mulig forhøjet belastning af tilløb til renseanlæg med miljøskadelige stoffer. 
The drainage water can be drained via a sewer system with potentially increased impact from environmentally harmful substances on inlets to sewage treatment plants.
Drænvand vil ved større regnskyl kunne afledes til nærliggende vandløb. 
During heavy showers, the drainage water may also be drained to adjacent watercourses.
Endvidere vil overskudsvand fra kloak ved kraftige regnskyl kunne udledes til vandmiljøet. 
Surplus water from the sewer may during heavy showers also be discharged to the aquatic environment.
Derfor er det valgt at vurdere afledning af overskudsdrænvand til et nærliggende vandløb efter TGDs standardmodeller, hvilket også er benyttet i en norsk miljøvurdering (T. 
It is thus decided to assess the drainage of surplus drainage water to a watercourse nearby in accordance with TGD's standard models, which were also used in a Norwegian environmental assessment (T.
Samtidig vurderes det mulige bidrag til drikkevandsforurening ud fra drænvandets koncentrationer af miljø og sundhedsskadelige stoffer, og der foretages et skøn med hensyn til, om der kan være forhøjet belastning af miljøskadelige stoffer i drænvand, der afledes til kloak. 
At the same time, the potential contribution to drinking water contamination is assessed based on the concentrations of environmentally harmful and hazardous substances, and it is estimated whether there may be an increased impact from environmentally harmful substances on drainage water drained to a sewer.
N;R50/53: Meget giftig for organismer, der lever i vand/Kan forårsage uønskede langtidsvirkninger i vandmiljøet. 
N;R50/53: Very toxic to aquatic organisms/May cause long-term adverse effects in the aquatic environment.
Udvaskning af zink vil forekomme som zinkioner - sandsynligvis som en zinkkloridopløsning, især i vinterperioden. 
The leaching of zinc will be in the form of zinc ions - probably as a zinc chloride solution, especially in the winter season.
I Tabel 8.1 er vist økotoksikologiske data for fisk, hvirvelløse dyr og alger. 
Table 8.1 shows ecotoxicological data for fish, invertebrates and algae.
Tabel 8.1 Økotoksikologiske data for opløst zink 
Table 8.1 Ecotoxicological data for dissolved zinc
EC50, 96 timer = 10 mg/l , EC10, 96 timer = 1 mg/l 
EC50, 96 hours = 10 mg/l , EC10, 96 timer = 1 mg/l
IUCLID dataset zinkklorid) 
IUCLID dataset zincchloride)
Opløseligheden af zinkklorid meget høj med en opløselighed på 4.320 g/l ved 25 °C. 
The solubility of zinc chloride is very high, the solubility being 4,320 g/l at 25°C.
Bioakkumulationsfaktoren for opløst zink i alger angives op til ca. BCF = 10.000, mens akkumulation i de fleste bløddyr er op til 500, bortset fra bløddyr, som lever i sediment, fx krabber med BCF op til 10.000 og østers op til 15.000 (IUCLID dataset zink). 
The bioaccumulation factor for dissolved zinc in algae is specified to be up to approx. BCF = 10,000, whereas the accumulation in most molluscs is up to 500, apart from molluscs living in sediment, e.g. crabs, with a BCF of up to 10,000 and oysters of up to 15,000 (IUCLID data set zinc).
For fisk er bioakkumulationen af opløst zink < 500 (IUCLID dataset zink). 
For fish, the bioaccumulation of dissolved zinc is < 500 (IUCLID data set zinc).
NOEC-værdien for alger giver med en vurderingsfaktor på 100 et mindste-effektniveau på PNEC = 0,5 µg/l. 
With an assessment factor of 100, the NOEC value for algae gives a no-effect concentration of PNEC = 0.5 µg/l.
I den norske miljøundersøgelse (T. 
In the Norwegian environmental study (T.
Källquist, 2005) er benyttet PNECvand = 3,1 µg/l ud fra et bedre datagrundlag i udkast til EU-risikovurdering af miljøeffekter for zink, hvorfor denne værdi benyttes til miljøvurderingen. 
Källquist, 2005), PNECwater = 3.1 µg/l was used based on a better data basis in a draft EU risk assessment of environmental effects for zinc, and this value is thus used in the environmental assessment.
Tabel 8.2 Økotoksikologiske data for 6PPD 
Table 8.2 Ecotoxicological data for 6PPD
Fordelingskoefficienten mellem oktanol og vand er log Kow = 5,4 (IUCLID dataset 6PPD), hvorfor der kan forventes bioakkumulation (risiko ved log Kow = 3). 
The distribution coefficient between octanol and water is log Kow = 5.4 (IUCLID data set 6PPD), for which reason bioaccumulation can be expected (risk at log Kow = 3).
Stoffet er ikke nedbrydeligt ud fra bionedbrydelighedstest. 
Biodegradation tests show that the substance is non-degradable.
En aerob bionedbrydelighedstest med aktiveret slam gav således 7,2 % nedbrydning efter 32 dage og en aerob test med husholdningsslam 13-40 % over 28 dage. 
An aerobic biodegradation test with activated sludge thus resulted in 7.2% degradation after 32 days and an aerobic test with household sludge resulted in 13-40% after 28 days.
Der er ikke fundet data for langtidsforsøg. 
No data have been found for long-term tests.
I Tabel 8.3 er vist økotoksikologiske data for fisk og alger. 
Table 8.3 shows ecotoxicological data for fish and algae.
Tabel 8.3 Økotoksikologiske data for dicyclohexylamin 
Table 8.3 Ecotoxicological data for dicyclohexylamine
Fordelingskoeeficient oktanol-vand log Kow = 3,5 (IUCLID dataset dicyclohexylamin). 
The distribution coefficient between octanol and water is log Kow = 3.5 (IUCLID data set dicyclohexylamine).
Vandopløseligheden er 800 mg/l, 25 °C. 
The water solubility is 800 mg/l, 25°C.
Stoffet er nemt nedbrydeligt ud fra bionedbrydelighedstest. 
Biodegradation tests show that the substance is easily degradable.
Aerobe bionedbrydelighedstest med husholdningsslam gav således > 90 % nedbrydning efter 20 dage ved en koncentration på 0,8 mg/l, og test i aktiveret slam gav 76,9 % nedbrydning efter 14 dage ved en stofkoncentration på 100 mg/l (IUCLID dataset dicyclohexylamin). 
Aerobic biodegradation tests with household sludge thus resulted in > 90% degradation after 20 days at a concentration of 0.8 mg/l, and tests in activated sludge resulted in 76.9% degradation after 14 days at a substance concentration of 100 mg/l (IUCLID data set dicyclohexylamine).
Der findes kun data for vækstforsøg med alger. 
Data are only available for algal growth tests.
Data for økotoksicitet er mangelfulde, da der ikke er data for hvirvelløse dyr. 
The data for ecotoxicity are inadequate as there are no data for invertebrates.
Fra vækstforsøget i tabellen på Scenedesmus subspicatus-alger blev angivet en NOEC = 0,016 mg/l med en LOEC på 0,031 mg/l, som kan benyttes til vurdering af kronisk effekt på alger i henhold til TGD. 
In the growth test of Scenedesmus subspicatus algae shown in the table, an NOEC of 0.016 mg/l was specified with an LOEC of 0.031 mg/l, which may be used in the assessment of chronic effect on algae in accordance with TGD.
Da der ikke findes data for hvirvelløse dyr, kan der ikke umiddelbart estimeres en PNEC. 
As no data are available for invertebrates, a PNEC cannot immediately be estimated.
For at supplere datagrundlaget ses på det beslægtede stof cyclohexylamin. 
To supplement the data basis, the related substance cyclohexylamine is reviewed.
Tabel 8.4 Økotoksikologiske data for cyclohexylamin 
Table 8.4 Ecotoxicological data for cyclohexylamine
(IUCLID dataset cyclohexylamin) 
(IUCLID dataset cyclohexylamine)
Stoffet viser korttidseffekter med LC50 for fisk på samme niveau som dicyclohexylamin. 
The substance shows short-term effects with LC50 for fish being at the same level as dicyclohexylamine.
Korttidseffekter for hvirvelløse dyr er på niveau med data for fisk, og data for alger tyder på nogenlunde samme giftighed for de to stoffer. 
The short-term effects for invertebrates are at the same level as the data for fish, and the data for algae suggest that the toxicity of the two substance is more or less the same.
Tabel 8.5 Økotoksikologiske data for diisobutylftalat 
Table 8.5 Ecotoxicological data for diisobutyl phthalate
Fordelingskoeeficient oktanol-vand log Kow= 4,11 (IUCLID dataset DIBP), hvorfor der kan forventes bioakkumulation (risiko ved log Kow = 3). 
The distribution coefficient between octanol and water is log Kow= 4.11 (IUCLID data set DIBP), for which reason bioaccumulation can be expected (risk at log Kow = 3).
Bioakkumulationsfaktorer for cyprinus carpio er ud fra modelberegninger angivet til 780. 
The bioaccumulation factors for cyprinus carpio are specified to be 780 based on model calculations.
Stoffet er let nedbrydeligt ud fra bionedbrydelighedstest. 
Biodegradation tests show that the substance is easily degradable.
For Daphnia magna er fundet NOEC = 1 mg/l i forsøg over 21 dage med LOEC = 3 mg/l (IUCLID dataset DIBP). 
For Daphnia magna, an NOEC of 1 mg/l was found in tests carried out over a 21-day period with LOEC = 3 mg/l (IUCLID data set DIBP).
25154-52-3, er klassificeret med: 
Nonylphenol, CAS no. 25154-52-3, classified as:
Tabel 8.6 Økotoksikologiske data for nonylphenol 
Table 8.6 Ecotoxicological data for nonylphenol
Fordelingskoeeficient oktanol-vand log Kow= 4,48 (Rar nonylphenol), hvorfor der kan forventes bioakkumulation (risiko ved over log Kow = 3). 
The distribution coefficient between octanol and water is log Kow= 4.48 (Rar nonylphenol), for which reason bioaccumulation can be expected (risk at values above log Kow = 3).
Bioakkumulationsfaktoren er i referencen angivet til 1280. 
In the reference, the bioaccumulation factor is specified to be 1280.
Stoffet er ikke let nedbrydeligt ud fra bionedbrydelighedstest. 
Biodegradation tests show that the substance is not easily degradable.
For fisk og ligeledes hvirvelløse dyr er NOEC fra langtidsforsøg angivet til mellem 1 og 10 µg/l, mens NOEC-værdien for alger er baseret på en EC10-værdi og sat til 3,3 µg/l (Rar nonylphenol). 
For fish and invertebrates, the NOEC from long-term tests is specified to be between 1 and 10 µg/l, whereas the NOEC value for algae is based on an EC10 value and put at 3.3 µg/l (Rar nonylphenol).
En aerob bionedbrydelighedstest med aktiveret slam og koncentration af stoffet på 34,5 mg/l viste 2 % nedbrydning efter 28 dage (IUCLID dataset 2,4-di-tert-butylphenol). 
An aerobic biodegradation test with activated sludge and a substance concentration of 34.5 mg/l exhibited 2% degradation after 28 days (IUCLID data set 2,4-di-tert-butylphenol).
Der findes ingen data for langtidsforsøg. 
No data have been found for long-term tests.
Da der kun er fundet data for fisk, kan der ikke umiddelbart estimeres en PNEC. 
As data have only been found for fish, a PNEC cannot immediately be estimated.
Der er derfor søgt data på beslægtede stoffer. 
A search for data on related substances has thus been carried out.
Tabel 8.8 Økotoksikologiske data for 2,6 di-tert-butylphenol 
Table 8.8 Ecotoxicological data for 2,6-di-tert-butylphenol
For phenol er angivet en PNEC 7,7 ug/l ud fra langtidseffekter over for fiskeyngel. 
For phenol, a PNEC of 7.7 ug/l has been specified based on long-term effects for fry.
Det antages, at alger, som for phenol, er de mindst følsomme organismer for stoffet 2,4-di-tert-butylphenol og det beslægtede stof 2,6-di-tert-butylphenol. 
As is the case for phenol, it is assumed that algae are the least sensitive organisms to the substance 2,4-di-tert-butylphenol and the related substance 2,6-di-tert-butylphenol.
Der er fundet følgende økotoksikologiske data: 
The following ecotoxicological data have been found:
(Der var i den norske undersøgelse estimeret en PNEC = 900 ug/l ud fra NOEC = EC10 for alger på 9 mg/l og en vurderingsfaktor på 10). 
(In the Norwegian study, a PNEC = 900 ug/l was estimated based on NOEC = EC10 for algae of 9 mg/l and an assessment factor of 10.)
Stoffet er en polymerstabilisator, som er fundet i meget høje koncentrationer i væske fra udvaskningsforsøg fra test af et kunstgræsprodukt. 
The substance is a polymer stabiliser found in very high concentrations in liquid from leaching tests of an artificial turf product.
Fordelingskoeeficient oktanol-vand log Kow= 0,35 (Brugsanvisning Lowilite 77). 
Distribution coefficient between octanol and water is log Kow= 0.35 (Instructions for use, Lowilite 77).
Der findes kun korttidsdata, hvoraf alger er den mest følsomme organisme. 
Only short-term data are available, showing that algae are the most sensitive organisms.
8.9 Estimering af effekt af udledte stoffer 
8.9 Estimate of effect of discharged substances
8.9.1 Udledte stofmængder i drænvand 
8.9.1 Discharged substances in drainage water
I det følgende beregnes mængden af stoffer fra gummigranulat og kunstgræsmåtte i drænvand over et år under forudsætning af, at de fundne koncentrationer fra udvaskningsforsøg er ligevægtskoncentrationer, som ikke falder med tiden. 
Below is a calculation of the amount of substances from rubber granules and artificial turf mat in drainage water for a one-year period, based on the assumption that the concentrations found from leaching tests are equilibrium concentrations which do not decrease over time.
Der er benyttet et areal af en boldbane på 8000 m² og nedbørsmængder på 702 mm/år ud fra DMIs statistik 1966-1990 for Østjylland. 
The calculation uses an area of a pitch of 8,000 m² and precipitation of 702 mm/year based on the Danish Meteorological Institute statistics 1966-1990 for East Jutland.
Mængden af kunstgræsmåtte er beregnet til 24 tons ud fra en gennemsnitsvægt af modtagne prøver på 3 kg/m², mens vægten af gummigranulat er sat til 100 tons pr. bane ud fra oplysninger under kortlægningen. 
The amount of artificial turf mat is calculated to be 24 tonnes based on an average weight of the samples received of 3 kg/m², whereas the weight of the rubber granules is put at 100 tonnes per pitch based on mapping information.
Tabel 8.10 Worst case-estimat af udledte mængder af stoffer fra en boldbane med elastisk fyldmateriale pr. år 
Table 8.10 Worst case estimate of discharged amounts of substances from a football pitch with elastic infill per year
Tabellen viser, at mindre end 1 % af zinkindholdet og op til 20 % af ftalatindholdet udvaskes over et år, hvis det antages, at udvaskningen foregår med samme effektivitet over et år som over 24 timer. 
The table shows that less than 1% of the zinc content and up to 20% of the phthalate content leach during a year, assuming that the leaching occurs with the same efficiency during a one-year period as during a 24-hour period.
Det er som nævnt i analyseafsnittet vurderet, at stofkoncentrationerne i kontaktvand er maksimale koncentrationer, der sandsynligvis er noget højere end de koncentrationer, som vil opnås i drænvand fra en boldbane. 
As mentioned in the analysis section, it is assessed that the substance concentrations in the contact water are maximum concentrations which are probably somewhat higher than the concentrations that will be obtained in drainage water from a football pitch.
Endvidere er det sandsynligt, at drænvandskoncentrationerne af ftalater vil falde med tiden, såfremt infill forbliver intakt over tid. 
In addition, the drainage water concentrations of phthalates will probably fall over time provided that the infills remain intact over time.
Nærmere undersøgelser er imidlertid nødvendige for at bekræfte dette. 
Further studies are, however, required to confirm this.
Tabel 8.11 Worst case-estimat af udledte mængder fra en boldbane fra kunstgræs pr. år 
Table 8.11 Worst case estimate of discharged amounts from artificial turf from a football pitch per year
Tabellen viser, at en stor del af ftalatindholdet og 158 % af nonylphenolen udvaskes over et år, hvis det antages, at udvaskningen foregår med samme effektivitet over et år som over 24 timer. 
The table shows that a large part of the phthalate content and 158% of the nonylphenol leach during a one-year period if it is assumed that the leaching occurs with the same efficiency during a one-year period as during a 24-hour period.
Endvidere er det sandsynligt, at drænvandskoncentrationerne af ftalater og nonylphenoler vil falde med tiden, såfremt infill forbliver intakt over tid. 
In addition, the drainage water concentrations of phthalates and nonylphenols will probably fall over time provided that the infills remain intact over time.
8.9.2 Udledning af afdræningsvand til vandløb 
8.9.2 Discharge of drainage water to watercourses
I den følgende modelberegning undersøges effekten af udledning af udvalgte stoffer til eventuelle vandløb nær fodboldbaner (lokale effekter). 
The following model calculation investigates the effect of the discharge of selected substances to any watercourses near football pitches (local effects).
Dette vil især være relevant under større regnskyl, hvor banens dræn ikke kan modtage al regnvand. 
This is particularly during heavy showers where the pitch's drainage system cannot take all the rainwater.
Beregningen er udført med samme forudsætninger som i den norske undersøgelse (T. 
The calculation is made under the same assumptions as the Norwegian study (T.
Afdræningsvandets koncentration Ceff antages at blive fortyndet 10 gange (f) ved tilledning til grøft/mindre vandløb som angivet default i TGD (Technical Guidance Document, 2003). 
The concentration of the drainage water Ceff is assumed to be diluted 10 times (f) when drained to a catchwater drain/small watercourse as specified as default in TGD (Technical Guidance Document, 2003).
Koncentrationen i vandfasen kan beregnes til: 
The concentration in the water phase can be calculated to be:
PECvand= Ceff /((1+Kpsusp x SUSPvand x 10-6)*f) 
PECwater = Ceff /((1+Kpsusp x SUSPwater x 10-6)*f)
hvor Kpsusp er fordelingskoeeficenten mellem faststof og vand beregnet fra KOC med et indhold af organisk stof i suspenderet materiale sat til default-værdien c org,susp= 10 %. 
where Kpsusp is the distribution coefficient between solid and water calculated from KOC with a content of organic substance in suspended material put at the default value c org,susp= 10%.
SUSPvand er koncentrationen af suspenderet materiale (mg/l) -værdien sættes til default-værdien 15 mg/l. 
SUSPwater is the concentration of suspended material (mg/l) - the value is put at the default value of 15 mg/l.
Koc beregnes ud fra Kow ud fra QSAR-modellen for ikke-hydrofobe organiske stoffer i TGD. 
Koc is calculated on the basis of Kow from the QSAR model for non-hydrophobic organic substances in TGD.
den volumenbaserede fordelingskoefficient af suspenderet materiale i forhold til vand Ksusp-vand (m³/m³) beregnes med modelværktøjet EUSES 2.0 med input af KOC og den valgte QSAR-model (EUSES 2.0). 
the volume-based distribution coefficient of suspended material in relation to water Ksusp-water (m³/m³) is calculated using the model tool EUSES 2.0 with input of KOC and the selected QSAR model (EUSES 2.0).
Endelig beregnes forholdene PECvand/PNECvand, samt PECsediment/PNECsediment 
Finally, the following ratios are calculated: PECwater/PNECwater as well as PECsediment/PNECsediment
(sikkerhedsmarginer) til at vurdere, om der er en mulig lokal miljøeffekt ved udledning af de undersøgte stoffer. 
(margins of safety) to assess whether there is a potential local environmental effect from discharge of the substances investigated.
I Tabel 8.12 er vist en worst case-beregning af miljøeffekten ved udledning af drænvand stammende fra elastisk fyldmateriale til et nærliggende vandløb, idet det antages, at afdræningsvandets koncentrationer af stoffer svarer til de fundne koncentrationer i kontaktvand. 
Table 8.12 shows a worst case calculation of the environmental effect of discharging drainage water from elastic infills to an adjacent watercourse, under the assumption that the drainage water concentrations of substances correspond to those found in contact water.
Tabel 8.12 beregning af udledning af udvaskede stoffer fra infill til vandløb 
Table 8.12 Calculation of discharge of leached substances from infills to watercourses
Som beskrevet i 8.9.1, er de fundne koncentrationer i kontaktvand worst case, idet koncentrationen af udvaskede stoffer må forventes at falde med tiden, ligesom den benyttede udvaskningsmetode skønnes at være mere effektiv med større væske-faststofkontakt end den reelle situation på en boldbane. 
As described in 8.9.1, the concentrations found in contact water are worst case scenarios as the concentration of leached substances must be expected to decrease over time just as the leaching method used is deemed to be more efficient with more liquid-solid contact than the actual situation on a football pitch.
Det skal her bemærkes, at en test i lysimeter formentlig underestimerer udvaskningen, da den fysiske påvirkning fra spillerne på en våd boldbane (under regnvejrsforhold) bør øge væske-faststofkontakten i forhold til et lysimeter, hvor der er ikke er en mekanisk påvirkning af banen fra fodboldspillerne. 
In this connection, it should be noted that a lysimeter test probably underestimates the leaching level as the physical impact from the players on a wet pitch (during rain) should increase the liquid-solid contact compared to a lysimeter where there is no mechanical impact on the pitch from the football players.
Tabel 8.12 viser, under forudsætning af en udvaskning fra elastisk infill under brug på en boldbane svarende til resultaterne fra udvaskningstesten, en effekt på nærliggende vandløb fra zink på niveau med resultaterne i den norske undersøgelse. 
Table 8.12 shows - based on the assumption that the leaching from elastic infills during use of a football pitch corresponds to the results from the leaching test - an effect on adjacent watercourses from zinc at a level corresponding to the result in the Norwegian study.
Tilsvarende koncentrationsniveauer ses for phenol, 2,4-bis(1,1-dimethylethyl)-. 
Similar concentration levels are observed for phenol, 2,4-bis(1,1-dimethylethyl)-.