Development of a method for the determination of phthalate esters in sewage sludge including chromatographic separation from polychlorinated biphenyls, pesticides and polyaromatic hydrocarbons

Zurmühl, Torsten

doi:10.1039/an9901501171

Cited by 20 publications

(5 citation statements)

References 20 publications

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“…The analysis of sewage sludge (four samples, year 1976, 1981, 1989, 1991) for PAH, NPE , PAE and LAS reveals concentrations varying between mg/kg to g/kg DW (figure 1). These concentrations fit the average values found for sewage sludge in Europe (Bennie et al, 1998;Webber and Lesage, 1989;Icon, 2001;Zurmuhl, 1990) with very high level of LAS (10 g/kg), medium level of NPE and PAE (200-500 mg/kg) and low level of PAH (mg/kg for the sum of 16 PAHs, Lichtfouse et al, 2005). However, these levels are all above the proposed limits of the third draft of the EU sewage sludge directive (EU, 2001), except for the PAHs.…”

Section: Resultssupporting

confidence: 82%

Fate of organic pollutants after sewage sludge spreading on agricultural soils: a 30-years field-scale recording

Patureau

Laforie

Lichtfouse

et al. 2007

Water Practice and Technology

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Toxic organic compounds, such as the surfactants linear alkylbenzene sulfonates (LAS) and nonylphenol polyethoxylates (NPE), Polycyclic aromatic hydrocarbons (PAH) and residues derived from plastics (PAE-phthalates) end up in sewage sludge. In order to evaluate and quantify the potential environmental risks associated with the xenobiotic introduction into biological life cycle, the EU BIOWASTE project (QLK5-CT-2002-01138) devotes one task to the study of the fate of xenobiotic in a sandy soil after sludge spreading on a 30-year field-scale record experiment. Experimental maize crop fields from Bordeaux (France) have been amended with 100 tons per hectare each 2 years from 1974 to 1992. From 1992 to 2004, the fields were maintained and cropped with maize. This experiment shows that the concentration fluctuations in the sludge amended soil follow the same pattern of those in the sewage sludge showing that there is a real impact of the present xenobiotics in the sewage sludge on the concentration of the xenobiotics in the soil. Nonetheless, 12 years after the last addition of sewage sludge, the residual concentrations remain from 2 to 10 times higher than the content of the control soil, even though these levels are inferior to the Predicted Non Effect Concentration (PNEC). Only LAS level went back to the level in the control soil. However, only the LAS concentration is above the PNEC during all the experiment due to the very high level of LAS in the sludge (20 g/kg dry weight). These results show that even though this compound is much more degradable than NPE and PAE, it may have a long term effect in soil if high quantities are spread. To conclude, this study underlines the importance to fix maximum level for xenobiotic compounds for sewage sludge spreading on agricultural land, and also the central role of the sewage sludge processes in reducing the xenobiotic concentrations before spreading.

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Section: Resultssupporting

confidence: 82%

Fate of organic pollutants after sewage sludge spreading on agricultural soils: a 30-years field-scale recording

Patureau

Laforie

Lichtfouse

et al. 2007

Water Practice and Technology

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“…The combined hexane extract was concentrated to a volume of 5 ml by evaporating the hexane in a fume hood at 40°C with a flow of N 2 . Subsequently, a column chromatography cleanup procedure was carried out partially as described by Zurmühl (25). The concentrated hexane extract was loaded onto 20-ml glass syringe chromatography columns containing 10 g of neutral alumina (Merck).…”

Section: Methodsmentioning

confidence: 99%

Degradation of Phthalate and Di-(2-Ethylhexyl)phthalate by Indigenous and Inoculated Microorganisms in Sludge-Amended Soil

Roslev

Madsen

Thyme

et al. 1998

Appl Environ Microbiol

101

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The metabolism of phthalic acid (PA) and di-(2-ethylhexyl)phthalate (DEHP) in sludge-amended agricultural soil was studied with radiotracer techniques. The initial rates of metabolism of PA and DEHP (4.1 nmol/g [dry weight]) were estimated to be 731.8 and 25.6 pmol/g (dry weight) per day, respectively. Indigenous microorganisms assimilated 28 and 17% of the carbon in [14C]PA and [14C]DEHP, respectively, into microbial biomass. The rates of DEHP metabolism were much greater in sludge assays without soil than in assays with sludge-amended soil. Mineralization of [14C]DEHP to 14CO2 increased fourfold after inoculation of sludge and soil samples with DEHP-degrading strain SDE 2. The elevated mineralization potential was maintained for more than 27 days. Experiments performed with strain SDE 2 suggested that the bioavailability and mineralization of DEHP decreased substantially in the presence of soil and sludge components. The microorganisms metabolizing PA and DEHP in sludge and sludge-amended soil were characterized by substrate-specific radiolabelling, followed by analysis of 14C-labelled phospholipid ester-linked fatty acids (14C-PLFAs). This assay provided a radioactive fingerprint of the organisms actively metabolizing [14C]PA and [14C]DEHP. The14C-PLFA fingerprints showed that organisms with different PLFA compositions metabolized PA and DEHP in sludge-amended soil. In contrast, microorganisms with comparable 14C-PLFA fingerprints were found to dominate DEHP metabolism in sludge and sludge-amended soil. Our results suggested that indigenous sludge microorganisms dominated DEHP degradation in sludge-amended soil. Mineralization of DEHP and PA followed complex kinetics that could not be described by simple first-order equations. The initial mineralization activity was described by an exponential function; this was followed by a second phase that was described best by a fractional power function. In the initial phase, the half times for PA and DEHP in sludge-amended soil were 2 and 58 days, respectively. In the late phase of incubation, the apparent half times for PA and DEHP increased to 15 and 147 days, respectively. In the second phase (after more than 28 days), the half time for DEHP was 2.9 times longer in sludge-amended soil assays than in sludge assays without soil. Experiments with radiolabelled DEHP degraders suggested that a significant fraction of the 14CO2 produced in long-term degradation assays may have originated from turnover of labelled microbial biomass rather than mineralization of [14C]PA or [14C]DEHP. It was estimated that a significant amount of DEHP with poor biodegradability and extractability remains in sludge-amended soil for extended periods of time despite the presence of microorganisms capable of degrading the compound (e.g., more than 40% of the DEHP added is not mineralized after 1 year).

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“…NM-medium without cells or with autoclaved cells was used as controls. After incubation, PAEs were extracted by adding 2 ml nhexane:ethylacetate (1:1) containing internal standards as suggested previously (Zurmu¨hl 1990). For liquid-liquid extractions, samples were shaken for 30 min and phases separated overnight.…”

Section: Mtbe and Pae Degradationmentioning

confidence: 99%

Degradation of organic pollutants by methane grown microbial consortia

Hesselsøe

Boysen²,

Iversen

et al. 2005

Biodegradation

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Microbial consortia were enriched from various environmental samples with methane as the sole carbon and energy source. Selected consortia that showed a capacity for co-oxidation of naphthalene were screened for their ability to degrade methyl-tert-butyl-ether (MTBE), phthalic acid esters (PAE), benzene, xylene and toluene (BTX). MTBE was not removed within 24 h by any of the consortia examined. One consortium enriched from activated sludge ("AAE-A2"), degraded PAE, including (butyl-benzyl)phthalate (BBP), and di-(butyl)phthalate (DBP). PAE have not previously been described as substrates for methanotrophic consortia. The apparent Km and Vmax for DBP degradation by AAE-A2 at 20 degrees C was 3.1 +/- 1.2 mg l(-1) and 8.7 +/- 1.1 mg DBP (g protein x h)(-1), respectively. AAE-A2 also showed fast degradation of BTX (230 +/- 30 nmol benzene (mg protein x h)(-1) at 20 degrees C). Additionally, AAE-A2 degraded benzene continuously for 2 weeks. In contrast, a pure culture of the methanotroph Methylosinus trichosporium OB3b ceased benzene degradation after only 2 days. Experiments with methane mono-oxygenase inhibitors or competitive substrates suggested that BTX degradation was carried out by methane-oxidizing bacteria in the consortium, whereas the degradation of PAE was carried out by non-methanotrophic bacteria co-existing with methanotrophs. The composition of the consortium (AAE-A2) based on polar lipid fatty acid (PLFA) profiles showed dominance of type II methanotrophs (83-92% of biomass). Phylogeny based on a 16S-rRNA gene clone library revealed that the dominating methanotrophs belonged to Methylosinus/Methylocystis spp. and that members of at least 4 different non-methanotrophic genera were present (Pseudomonas, Flavobacterium, Janthinobacterium and Rubivivax).

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Development of a method for the determination of phthalate esters in sewage sludge including chromatographic separation from polychlorinated biphenyls, pesticides and polyaromatic hydrocarbons

Cited by 20 publications

References 20 publications

Fate of organic pollutants after sewage sludge spreading on agricultural soils: a 30-years field-scale recording

Fate of organic pollutants after sewage sludge spreading on agricultural soils: a 30-years field-scale recording

Degradation of Phthalate and Di-(2-Ethylhexyl)phthalate by Indigenous and Inoculated Microorganisms in Sludge-Amended Soil

Degradation of organic pollutants by methane grown microbial consortia

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