Low Temperature, Autotrophic Microbial Denitrification Using
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Biodegradation DOI 10.1007/s10532-017-9796-7 ORIGINAL PAPER Low temperature, autotrophic microbial denitrification using thiosulfate or thiocyanate as electron donor Elias Broman . Abbtesaim Jawad . Xiaofen Wu . Stephan Christel . Gaofeng Ni . Margarita Lopez-Fernandez . Jan-Eric Sundkvist . Mark Dopson Received: 14 March 2017 / Accepted: 22 May 2017 Ó The Author(s) 2017. This article is an open access publication Abstract Wastewaters generated during mining and nitrate, and thiocyanate, along the need to increase processing of metal sulfide ores are often acidic production from sulfide mineral mining calls for low (pH \ 3) and can contain significant concentrations of cost techniques to remove these pollutants under nitrate, nitrite, and ammonium from nitrogen based ambient temperatures (approximately 8 °C). In this explosives. In addition, wastewaters from sulfide ore study, we used both aerobic and anaerobic continuous treatment plants and tailings ponds typically contain cultures to successfully couple inorganic sulfur com- large amounts of inorganic sulfur compounds, such as pound (i.e. thiosulfate and thiocyanate) oxidation for thiosulfate and tetrathionate. Release of these wastew- the removal of nitrogenous compounds under neutral aters can lead to environmental acidification as well as to acidic pH at the low temperatures typical for boreal an increase in nutrients (eutrophication) and com- climates. Furthermore, the development of the respec- pounds that are potentially toxic to humans and tive microbial communities was identified over time animals. Waters from cyanidation plants for gold by DNA sequencing, and found to contain a consor- extraction will often conjointly include toxic, sulfur tium including populations aligning within Flavobac- containing thiocyanate. More stringent regulatory terium, Thiobacillus, and Comamonadaceae lineages. limits on the release of mining wastes containing This is the first study to remediate mining waste waters compounds such as inorganic sulfur compounds, by coupling autotrophic thiocyanate oxidation to nitrate reduction at low temperatures and acidic pH by means of an identified microbial community. Electronic supplementary material The online version of this article (doi:10.1007/s10532-017-9796-7) contains supple- mentary material, which is available to authorized users. Keywords Biodegradation Á Eutrophication Á Inorganic sulfur compound Á Sulfide mineral Á E. Broman (&) Á A. Jawad Á X. Wu Á S. Christel Á G. Ni Á M. Lopez-Fernandez Á M. Dopson Wastewater Centre for Ecology and Evolution in Microbial Model Systems (EEMiS), Linnaeus University, Kalmar, Sweden e-mail: [email protected] J.-E. Sundkvist Introduction Boliden Mineral AB, 936 81 Boliden, Sweden Wastewaters generated during mining and processing Present Address: of metal sulfide ores can contain significant concen- X. Wu Department of Biology, University of Copenhagen, Univer- trations of nitrogenous compounds. These include - - sitetsparken 15, 2100 Copenhagen, Denmark nitrate (NO3 ), nitrite (NO2 ), and ammonium 123 Biodegradation ? ? - (NH4 ) that are derived from nitrogen based explo- typically consists of nitrification (NH4 and NO2 - sives, such as ‘ammonium nitrate fuel oil’ (ANFO) conversion to NO3 ) followed by denitrification that and watergel-based explosives (Revey 1996). It has couples oxidation of an electron donor [e.g. organic 2? 2- - been reported that 0.2 to 28% of explosives are carbon, ferrous iron (Fe ), or sulfide (S )] to NO3 undetonated during blasting (best practice is 2–5% for reduction that if completely reduced, eventually forms ANFO) (Morin and Hutt 2009) and if the nitrogenous nitrogen gas (Lu et al. 2014). Recent work has compounds are released, they cause eutrophication in confirmed that organic carbon compounds such as water bodies. Some consequences of eutrophication methanol and acetate favor specific denitrifying bac- - are an increase in oxygen demand that results in teria and successfully removes NO3 (Li et al. 2016a). recipient waters turning anoxic (Conley et al. 2011), However, the use of methanol as an electron donor possible hazards to human health (Knobeloch et al. produces CaCO3, which increases the pH, and affects 2000), and potential toxicity to aquatic animals the denitrifying microbial community in the system. (Alonso and Camargo 2003). In addition to nitroge- For example, it has been observed that up to 22.3% of - nous pollutants, some mining wastewaters are rich in the NO3 concentration in a methanol fed bioreactor - inorganic sulfur compounds (ISCs). These compounds accumulated as NO2 while increasing the pH up to - - can include toxic thiocyanate (SCN ) generated from 9.2. In contrast, at pH 7.6 the accumulation of NO2 cyanide used in gold extraction (Zagury et al. 2004). A was negligible (Li et al. 2016b). Biological nitrogen further major ISC typically found in mining wastew- removal in wetlands or reactive barriers functions by 2- aters is thiosulfate (S2O3 ) that can be generated promoting denitrification processes in sediments or from for example, hydrogen sulfide added during buried organic matter, respectively (Batty and molybdenum flotation (Liljeqvist et al. 2011), ammo- Younger 2004). Nitrogen removal has also been niacal thiosulfate leaching (Grosse et al. 2003), and demonstrated in bioreactors with organic (e.g. Papirio dissolution of metal sulfides such as pyrite (Eq. 1) et al. 2014; Zou et al. 2014) and inorganic electron (Dopson and Johnson 2012; Schippers and Sand donors including ISCs (e.g. Chung et al. 2014;Di 1999). Complete oxidation of ISCs generates sulfuric Capua et al. 2015; Zhang et al. 2009; Zou et al. 2016). 2- acid (Eq. 2) that results in serious environmental Other studies investigating S2O3 oxidation coupled - damage if released due to acidification of recipient with NO3 reduction utilized pure cultures of water bodies in a process termed ‘acid mine drainage’, Thiobacillus denitrificans (Justin and Kelly 1978a, b) abbreviated as AMD (Chen et al. 2016). and Sulfurimonas denitrificans [originally named - 3þ 2À 2þ þ Thiomicrospira denitrificans (Hoor 1975)]. SCN FeS2 þ 6Fe þ 3H2O ! S2O3 þ 7Fe þ 6H - oxidation can also be linked to NO3 reduction by ð1Þ the soda-lake sediment dwelling species Thialkalivib- rio thiocyanodenitrificans (Sorokin et al. 2004). In 2À 3þ 2À 2þ S2O3 þ 8Fe þ 5H2O ! 2SO4 þ 8Fe some microorganisms, SCN- þ can act as an electron þ 10H ð2Þ donor as well as providing sulfur and nitrogen to the - A complicating factor in treating mining wastew- cell (Ogawa et al. 2013). Finally, a novel SCN aters in cold climates, such as in northern Sweden, is degrading pathway has been identified by metage- that the water temperature rarely increases above nomics in a Thiobacillus-like strain (Kantor et al. approximately 15 °C (Liljeqvist et al. 2011). Due to 2015). Advantages of ISC fed autotrophic versus economic constraints, this requires the development of heterotrophic denitrification are that less sludge is (bio)remediation processes for contaminant removal produced and costs are reduced as an organic electron that operate at low temperatures. donor does not need to be added. A disadvantage is the High concentrations of nitrogen compounds such as reduced pH due to generation of sulfuric acid (Eq. 2). ? - However, efficient autotrophic, ISC-fed, low temper- NH4 and NO3 in mining waters can be treated by physical (e.g. membrane separation), chemical (e.g. ature denitrification systems for thiocyanate removal electrochemical removal), and biological (e.g. nitrifi- remain to be developed. cation and denitrification) methods (reviewed in To be able to increase production from sulfide Jermakka et al. 2015). Biological nitrogen removal mineral mining coupled to more stringent regulatory 123 Biodegradation - limits on the release of ISCs and NO3 , low cost Table 2 An overview of the experimental design of the aer- techniques to remove these pollutants under ambient obic R1 and anaerobic R2 SCN- fed bioreactors temperatures are required. In this study, autotrophic Days °CpH ISC oxidation coupled to removal of nitrogenous compounds was investigated at low temperature. In 0–231 21 8.0–8.5 addition, the structures of the microbial communities 232–300 15 8.0–8.5 were identified by DNA sequencing. 301–338 10 8.0–8.5 339–448 8 8.0–8.5 449–510 8 5.5 Materials and methods 511–524 8 3.5 Temperature and pH were lowered throughout the experiment Bioreactor set-up Continuous culture bioreactors (500 mL working PALL Corporation), respectively. The reactors were volume) were operated with a basal salts medium inoculated with water sampled from a municipal plus nitrate as electron acceptor. The feed medium was wastewater treatment plant (Tuvanverket), Skelleftea˚, autoclaved before filter sterilized (0.2 lm membrane Sweden. The temperature in the bioreactors was filter; Sarstedt, Nu¨mbrecht, Germany) ISCs were lowered over time: day 0–231 at 21 °C; 232–300 at added, i.e. thiosulfate (0.89 mM) for a thiosulfate 15 °C; 301–337 at 10 °C; followed by 8 °C until the reactor and thiocyanate (6.88 mM) for the aerobic and end of the experiment. In addition, the pH was lowered anaerobic reactors (Table 1). For both experiments with 4.6 M H2SO4 to 5.5 at day 448 and then to 3.8 at (described below), the retention time was 9 h and the day 510. initial pH in the bioreactors was adjusted to 8.0–8.5 by addition of 1 M Na2CO3. Microbial biomass was Thiosulfate fed bioreactor retained in the reactors by promoting biofilm growth 2- on 50% (vol/vol) autoclaved high surface area biofilm The S2O3 fed bioreactor (R3) was maintained at carriers (AnoxKaldnes). The bioreactors and medium 8 °C and operated between February 11th 2013 and feed were maintained at the desired temperature by December 16th 2013 (308 days) in microaerophilic placing them in a constant temperature room. conditions i.e. the reactor was not sparged with air and the medium was stirred gently with a magnetic Thiocyanate fed bioreactors flea such that the surface of the medium was not broken. The bioreactor was inoculated with a Two SCN- fed bioreactors were operated between sediment sample removed from an AMD stream June 3rd 2014 and November 9th 2015 (totaling 250 m below ground in the Boliden operated 524 days; Table 2).