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Long-Term Ferrocyanide Application Via Deicing Salts Promotes the Establishment of Actinomycetales Assimilating Ferrocyanide-Derived Carbon in Soil

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Long-Term Ferrocyanide Application Via Deicing Salts Promotes the Establishment of Actinomycetales Assimilating Ferrocyanide-Derived Carbon in Soil bs_bs_banner Long-term ferrocyanide application via deicing salts promotes the establishment of Actinomycetales assimilating ferrocyanide-derived carbon in soil Silvia Gschwendtner,1 Tim Mansfeldt,2 soils, belonging mostly to Actinomycetales Susanne Kublik,1 Evangelia Touliari,1 (Kineosporia, Mycobacterium, Micromonosporaceae). Franz Buegger3 and Michael Schloter1,* In the soil without pre-exposition, bacteria belonging 1Research Unit Environmental Genomics, Helmholtz to Acidobacteria (Gp3, Gp4, Gp6), Gemmatimonade- Zentrum Munchen,€ German Research Center for tes (Gemmatimonas)andGammaproteobacteria Environmental Health (GmbH), Ingolstadter€ Landstraße 1, (Thermomonas, Xanthomonadaceae)usedferro- Neuherberg 85764, Germany. cyanide as C source but not the present Actinomyc- 2Department Geowissenschaften, Bodengeographie/ etales. This indicated that (i) various bacteria are able Bodenkunde, Universitat€ zu Koln,€ Albertus-Magnus- to assimilate ferrocyanide-derived C and (ii) long-term Platz, Koln€ 50923, Germany. exposition to ferrocyanide applied with deicing salts 3Institute of Biochemical Plant Pathology, Helmholtz leads to Actinomycetales outcompeting other microor- Zentrum Munchen,€ German Research Center for ganisms for the use of ferrocyanide as C source. Environmental Health (GmbH), Ingolstadter€ Landstraße 1, Neuherberg 85764, Germany. Introduction Cyanide is produced by various organisms including Summary bacteria, algae, fungi and higher plants as defence Cyanides are highly toxic and produced by various mechanism or offensive strategy (Møller and Seigler, microorganisms as defence strategy or to increase 1998; Gallagher and Manoil, 2001; Zagrobelny et al., their competitiveness. As degradation is the most 2008) and consequently occurs naturally at low levels in efficient way of detoxification, some microbes devel- the environment. However, it is highly toxic for living oped the capability to use cyanides as carbon and organisms by complexing metalloproteins, e.g. cyto- nitrogen source. However, it is not clear if this chrome oxidase, and thus inhibiting protein function potential also helps to lower cyanide concentrations (Solomonson, 1981). Besides, cyanide severs nutrient in roadside soils where deicing salt application leads limitation in the environment by the formation of very to significant inputs of ferrocyanide. The question stable metal-cyanide complexes making essential nutri- remains if biodegradation in soils can occur without ents unavailable to organisms. Thus, organisms growing previous photolysis. By conducting a microcosm in the presence of cyanide must have an alternative cya- experiment using soils with/without pre-exposition to nide-insensitive metabolism (Junemann,€ 1997; Berthold road salts spiked with 13C-labelled ferrocyanide, we et al., 2000; Richardson, 2000) and/or the capacity to were able to confirm biodegradation and in parallel degrade cyanide to harmful molecules that can be used to identify bacteria using ferrocyanide as C source as C and N source. As the latter offers an additional via DNA stable isotope probing (DNA-SIP), TRFLP advantage in nutrient limited environments, the capacity fingerprinting and pyrosequencing. Bacteria assimi- for cyanide biodegradation is widespread among soil lating 13C were highly similar in the pre-exposed microorganisms (Dubey and Holmes, 1995) and can occur via four pathways: (i) via hydrolysis, generating either formamide or formate and ammonia, (ii) via oxida- Received 13 October, 2015; revised 18 March, 2016; accepted 28 tive degradation, generating CO and ammonia, (iii) via March, 2016. *For correspondence. E-mail schloter@helmholtz- 2 muenchen.de; Tel. +49(0)89 31872304; Fax +49(0)89 31872136 reduction, generating methane and ammonia and (iv) via Microbial Biotechnology (2016) 0(0), 000–000 substitution, producing thiocyanate (Raybuck, 1992). It is doi:10.1111/1751-7915.12362 postulated that in various environments close ‘microcy- Funding Information ’ We gratefully acknowledge Ludwig Niebrugge,€ Strassen, NRW cles of cyanogenic organisms and organisms assimilat- (Germany) for providing access to the roadside soils and Dr. Franz ing cyanide as C and N source exist, depending on € € 13 Gotzfried, Sudsalz AG (Germany) for supplying the C-labelled species composition and distribution (Allen and Strobel, ferrocyanide salt. Moreover, we thank Conny Galonska for nucleic acid extraction. 1966; Thatcher and Weaver, 1976). ª 2016 The Authors. Microbial Biotechnology published by John Wiley & Sons Ltd and Society for Applied Microbiology. This is an open access article under the terms of the Creative Commons Attribution License, which permits use, distribution and reproduction in any medium, provided the original work is properly cited. 2 S. Gschwendtner et al. In contrast to naturally occurring cyanide, anthro- question remains if the reported biodegradation of metal- pogenic activities produce large amounts of cyanide-con- cyanides is more a function of the dissociation of the taining wastes entering the environment via disposal of complex than of the microbial degradation. gas-purifier wastes from former manufactured gas or Despite its ecological significance, data on the fate and coke-oven plants (Mansfeldt et al., 1998; Wehrer et al., biodegradation of ferrocyanide complexes in soils are 2011), landfilling of blast-furnace and sewage sludge missing so far. We hypothesize (i) that the microbial (Mansfeldt and Dohrmann, 2001; Rennert et al., 2007), degradation will take place and that several soil microor- soil amendment with paper de-inking sludge (Mansfeldt, ganisms are able to use ferrocyanide as C source as this 2001) and waste water from mining and electroplating offers an additional advantage in nutrient limited environ- industry (Korte et al., 2000; Wong-Chong et al., 2006). ments. We postulate further (ii) that the microbial commu- Most of the released cyanide is complexed with iron as nity in pre-exposed roadside soils is adapted to II 4À III 3À ferrocyanide (Fe (CN)6 ) or ferricyanide (Fe (CN)6 ). ferrocyanide application, and consequently, microorgan- Another significant release of metal-cyanide complexes isms capable to assimilate ferrocyanide-derived C are into the environment is the application of deicing salt con- enriched when compared with a first exposed control soil. taining ferrocyanide as anticaking agent (Paschka et al., To test these hypotheses, we conducted a microcosm À1 1999). In Germany, currently about 100 mg Fe(CN)6 kg experiment using two roadside soils with pre-exposition to road salt are used, resulting in an annual input of 75– deicing salt and a control soil with a comparable soil tex- 425 Mg cyanide to the road soil environment. However, ture, which was collected in a wider distance to the road, the fate of ferrocyanide added via deicing salts into the thus not influenced by the deicing treatments. We used environment remains unclear. Although iron-cyanide com- 13C-labelled ferrocyanide and incubated the microcosms plexes are very stable in the dark and thus have low toxi- in the dark to prevent light-mediated dissociation. By this city in soil per se, they dissociate rapidly (8% hÀ1) when we were able (i) to show whether biodegradation occurs exposed to daylight (Meeussen et al., 1992), e.g. by and (ii) to identify microorganisms assimilating C derived transport of contaminated groundwater to the surface, from ferrocyanide complexes using DNA stable isotope releasing extremely toxic free cyanide. Several factors probing (DNA-SIP) combined with 16S rRNA amplicon- favour the adsorption (and consequently immobilization) based TRFLP fingerprinting and pyrosequencing. Our of metal-cyanide complexes to soil components, e.g. low results revealed 13C incorporation into microbial biomass pH, free iron oxide content, high clay content and high C as well as into DNA, indicating microbial degradation of organic matter content (Alesii and Fuller, 1976; Sut et al., the applied ferrocyanide. Although microbial community 2013). Coincidentally, Ohno (1990) found up to 200 lg structure differed significantly among all soils, bacteria total cyanide LÀ1 in adjacent surface waters (< 30 m) using ferrocyanide as C source were similar in the soils near uncovered salt storage facilities in Maine, USA. pre-exposed to deicing salts but differed highly when From simple soil sorption studies and the observation that compared with the soil without pre-exposition. Detailed measured cyanide surface water concentrations were differences in microbial community composition and 13C lower than predicted ones, the authors concluded that assimilation among the soils are discussed. adsorption had lowered cyanide concentrations in the soil during passage, indicating significant buffer capacity of Results soils. Despite its chemical stability, several studies Microbial incorporation of 13C derived from ferrocyanide reported microbial degradation of metal-cyanide com- plexes by various soil microorganisms, using it as N and/ Isotopic enrichment of microorganisms using ferro- or C source for growth (Aronstein et al., 1994; Barclay cyanide as additional C source for growth was per- et al., 1998a,b; Dursun et al., 1999; Yanase et al., 2000; formed in a microcosm experiment using soils from two Kwon et al., 2002). Biodegradation was found to be roadsides (D, F) with pre-exposition to deicing salts and mainly dependent on the physical nature of soils influenc- one control soil (W) without pre-exposition to deicing 13 ing substrate availability and on the availability of
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