Adaptation of Estuarine Ecosystems to the Biodegradation of Nitrilotriacetic Acid: Effects of Preexposure

Pfaender, Frederic K.; Shimp, Robert J.; Larson, Robert J.

doi:10.1897/1552-8618(1985)4[587:aoeett]2.0.co;2

Cited by 14 publications

(21 citation statements)

References 10 publications

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“…It is also possible that a longer lag period may be required for adaptation of carbofuran-degraders to this low level of carbofuran. One estuarine sample showed a slow linear breakdown of 10 ng.ml-' NTA until 50 d following a first treatment, after which the rate of degradation gradually increased, indicating adaptation of NTA-degraders [19]. The soil in the present study was retreated after only 30 d and then the degradation was followed for only another 8 d.…”

Section: Enumeration Of Microorganismsmentioning

confidence: 47%

“…Similarly, 1 pg.g-' of butylphenyl methylcarbamate was slowly degraded in soil, but the degradation of higher levels indicated microbial acclimation [26]. In sediment water cores pre-exposed to 10 ng.ml-' p-nitro-phenol, the degradation of 10 ng.ml-I p-nitrophenol was not enhanced [ 11, and some estuarine samples pre-exposed to low level of nitrilotriacetic acid (NTA) did not show adaptation to the degradation of 10 ng-ml-' NTA [19].…”

Section: Enumeration Of Microorganismsmentioning

confidence: 99%

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Soil Biodegradation of Carbofuran and Furathiocarb Following Soil Pretreatment With These Pesticides

Hendry¹,

Richardson²

1988

Environ Toxicol Chem

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A field application level (9 pg .g-') of carbofuran was completely hydrolyzed within 1 to 3 days in a loamy sand soil pretreated with the same level of carbofuran, while <5% of the carbofuran was hydrolyzed in control soil not pretreated. The number of microbial carbofuranhydrolyzers was substantially greater in loamy sand soil treated twice with a field application level (9 pg.g-') of carbofuran than in untreated soil. Also, carbofuran-adapted soil showed no significant change in the number of carbofuran-hydrolyzers during the period of rapid degradation. Inorganic nitrogen, at a typical fertilization level, appeared to slightly stimulate the enhanced degradation of carbofuran in the pretreated soil. Soil pretreated with an application level hydrolyzed 65% of a residue level (8 ng.g-') within two days, but virtually none of the remaining carbofuran was hydrolyzed thereafter. A microbial biomass carbon experiment with a sandy loam soil indicated that only 0.2% of the applied carbonyl-C could be attributed to biomass. Soil pretreated with a residue level did not show rapid degradation of the same level or a field application level, although the field application level was degraded slightly faster in this soil than in soil not pretreated. Soil pretreated with a field application level of carbofuran or furathiocarb also rapidly hydrolyzed the same level of furathiocarb, but furathiocarb is probably converted into carbofuran before hydrolysis.

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Section: Enumeration Of Microorganismsmentioning

confidence: 47%

Section: Enumeration Of Microorganismsmentioning

confidence: 99%

Soil Biodegradation of Carbofuran and Furathiocarb Following Soil Pretreatment With These Pesticides

Hendry¹,

Richardson²

1988

Environ Toxicol Chem

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“…Whereas Kirk and co-workers [121] found no NTA degradation by a marine bacterial population in coastal marine waters under aerobic or anoxic conditions, several other researchers found NTA degradation in estuarine and o¡shore environments [122^124]. In particular, in samples from an estuarine system which had been pre-exposed to NTA for several years, NTA was rapidly degraded with no lag period at the low NTA concentration of 10 Wg l 31 [123].…”

Section: In the Aquatic Environmentmentioning

confidence: 99%

Environmental fate and microbial degradation of aminopolycarboxylic acids

Bucheli-Witschel¹

2001

FEMS Microbiology Reviews

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Aminopolycarboxylic acids (APCAs) have the ability to form stable, water-soluble complexes with di- and trivalent metal ions. For that reason, synthetic APCAs are used in a broad range of domestic products and industrial applications to control solubility and precipitation of metal ions. Because most of these applications are water-based, APCAs are disposed of in wastewater and reach thus sewage treatment plants and the environment, where they undergo abiotic and/or biotic degradation processes. Recently, also natural APCAs have been described which are produced by plants or micro-organisms and are involved in the metal uptake by these organisms. For the two most widely used APCAs, nitrilotriacetate (NTA) and ethylenediaminetetraacetate (EDTA), transformation and mineralisation processes have been studied rather well, while for other xenobiotic APCAs and for the naturally occurring APCAs little is known on their fate in the environment. Whereas NTA is mainly degraded by bacteria under both oxic and anoxic conditions, biodegradation is apparently of minor importance for the environmental fate of EDTA. Photodegradation of iron(III)-complexed EDTA is supposed to be mostly responsible for its elimination. Isolation of a number of NTA- and EDTA-utilising bacterial strains has been reported and the spectrum of APCAs utilised by the different isolates indicates that some of them are able to utilise a range of different APCAs whereas others seem to be restricted to one compound. The two best characterised obligately aerobic NTA-utilising genera (Chelatobacter and Chelatococcus) are members of the alpha-subgroup of Proteobacteria. There is good evidence that they are present in fairly high numbers in surface waters, soils and sewage treatment plants. The key enzymes involved in NTA degradation in Chelatobacter and Chelatococcus have been isolated and characterised. The two first catabolic steps are catalysed by a monooxygenase (NTA MO) and a membrane-bound iminodiacetate dehydrogenase. NTA MO has been cloned and sequenced and its regulation as a function of growth conditions has been studied. Under denitrifying conditions, NTA catabolism is catalysed by a NTA dehydrogenase. EDTA breakdown was found to be initiated by a MO also which shares many characteristics with NTA MO from strictly aerobic NTA-degrading bacteria. In contrast, degradation of [S,S]-ethylenediaminedisuccinate ([S,S]-EDDS), a structural isomer of EDTA, was shown to be catalysed by an EDDS lyase in both an EDTA degrader and in a NTA-utilising Chelatococcus strain. So far, transport of APCAs into cells has only been studied for EDTA and the results obtained give strong evidence for an energy-dependent carrier system and Ca(2+) seems to be co-transported with EDTA. Due to their metal-complexing capacities, APCAs occur in the environment mostly in the metal-complexed form. Hence, the influence of metal speciation on various degradation processes is of utmost importance to understand the environmental behaviour of these compounds. In case of biodegradation, th...

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“…An understanding of the kinetics of biodegradation by subsurface microbes would contribute to our ability to predict the persistence of organic compounds in contaminated aquifers. The biodegradation of organic chemicals by natural microbial communities is a major means by which these compounds are removed from the environment [8,9]. The heterotrophic activity approach, suggested by Parsons and Strickland [lo] and modified by Wright and Hobbie [11,12], has recently been applied to the measurement of microbial degradative activity in aquatic [13][14][15] and soil environments .…”

Section: Soilmentioning

confidence: 99%

Aerobic Biodegradation of Natural and Xenobiotic Organic Compounds by Subsurface Microbial Communities

Swindoll¹,

Aelion²,

Dobbins³

et al. 1988

Environ Toxicol Chem

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Studies were conducted to characterize the diversity of degradative abilities of microbial communities from pristine aquifer solids samples. Biodegradation was measured in aquifer solids slurries as both the conversion of radiolabeled substrate to I4CO2 and the incorporation of label into cell biomass. Under aerobic conditions, the microbial community metabolized the following naturally occurring compounds: acetic acid, amino acids, cellulose, cinnamic acid, glucosamine and glucose. The xenobiotic compounds aniline hydrochloride, chlorobenzene, p-chlorophenol, rn-cresol, ethylene dibromide, naphthalene, phenol, toluene and trichlorobenzene were also biodegraded. Several kinetic parameters were calculated from the uptake and mineralization data.First-order rate constants ( K l ) ranged from lo-' to h-' for the natural compounds and from low3 to 10W6 h-' for the xenobiotic compounds. Turnover times ranged from 47 to more than 1,900 h for natural compounds and from 806 to 60,000 h for xenobiotic compounds. For some compounds, respiratory enzymes became saturated, whereas incorporation into biomass was firstorder. The results show that uptake into cell biomass represents a large fraction of total metabolism for many of the xenobiotic compounds. ''C-most-probable-number (MPN) of substrate degraders was calculated. MPNs for naturally occurring compounds ranged from 10' to lo6 per gram of soil. There were generally fewer than 10 xenobiotic degraders per gram of soil. The biodegradative activity of the subsurface community appears to differ in both rate and product distribution from the activities of aquatic or surface-soil communities.

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Adaptation of Estuarine Ecosystems to the Biodegradation of Nitrilotriacetic Acid: Effects of Preexposure

Cited by 14 publications

References 10 publications

Soil Biodegradation of Carbofuran and Furathiocarb Following Soil Pretreatment With These Pesticides

Soil Biodegradation of Carbofuran and Furathiocarb Following Soil Pretreatment With These Pesticides

Environmental fate and microbial degradation of aminopolycarboxylic acids

Aerobic Biodegradation of Natural and Xenobiotic Organic Compounds by Subsurface Microbial Communities

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