ORIGINAL RESEARCH article
Volume 8 - 2017 | https://doi.org/10.3389/fmicb.2017.02423
Characterizing Isozymes of Chlorite Dismutase for Water Treatment
- Department of Civil Environmental Engineering, University of Illinois at Urbana–Champaign, Urbana, IL, United States
This work investigated the potential for biocatalytic degradation of micropollutants, focusing on chlorine oxyanions as model contaminants, by mining biology to identify promising biocatalysts. Existing isozymes of chlorite dismutase (Cld) were characterized with respect to parameters relevant to this high volume, low-value product application: kinetic parameters, resistance to catalytic inactivation, and stability. Maximum reaction velocities (Vmax) were typically on the order of 104 μmol min-1 (μmol heme)-1. Substrate affinity (Km) values were on the order of 100 μM, except for the Cld from Candidatus Nitrospira defluvii (NdCld), which showed a significantly lower affinity for chlorite. NdCld also had the highest susceptibility to catalytic inactivation. In contrast, the Cld from Ideonella dechloratans was least susceptible to catalytic inactivation, with a maximum turnover number of approximately 150,000, more than sevenfold higher than other tested isozymes. Under non-reactive conditions, Cld was quite stable, retaining over 50% of activity after 30 days, and most samples retained activity even after 90–100 days. Overall, Cld from I. dechloratans was the most promising candidate for environmental applications, having high affinity and activity, a relatively low propensity for catalytic inactivation, and excellent stability.
Micropollutants and other emerging contaminants are challenging to remediate due to their diverse chemical structures, their persistence in the environment, the toxicity of some degradation products, and their ability to cause toxic effects at low concentrations. Recent studies have proposed the removal of emerging contaminants through novel biocatalytic approaches, in which biological enzymes are used in the absence of cells as catalysts (Hutchison et al., 2013; Chen et al., 2016; Martínez et al., 2017; Yang et al., 2017). Potential advantages of this approach include targeted, complete degradation even in complex environmental matrices and at low concentrations. Some biological enzymes also provide less specific catalytic activities that may have applications in remediation, as shown for example for unspecific peroxygenases derived from fungi (Karich et al., 2017). However, environmental applications require greater stability of the biocatalysts than is typically needed in applications with high-value products, such as pharmaceutical production (Hutchison et al., 2017). This work investigated possible biocatalysts for chlorite degradation in water treatment applications.
Chlorite is regulated by the United States Environmental Protection Agency at 1 mg L-1 in drinking water, while the World Health Organization has set a provisional guideline of 0.7 mg L-1 (World Health Organization, 2005). The health effects of chlorite, similar to those of nitrite, arise primarily through oxidative damage to red blood cells (World Health Organization, 2005). Chlorite is produced in drinking water when chlorine dioxide is used as a disinfectant (Richardson and Postigo, 2012) and in industrial processes such as wood pulp processing (World Health Organization, 2005). Chlorite could also be produced from incomplete degradation of other chlorine oxyanions like chlorate and the endocrine-disruptor perchlorate. Existing treatment methods for chlorite removal require addition of ferrous iron or thiosulfate and are sensitive to pH (World Health Organization, 2005). In contrast, the enzyme chlorite dismutase (Cld) converts chlorite into chloride and molecular oxygen via an intramolecular redox reaction, not requiring any external electron donor (van Ginkel et al., 1996).
For environmental applications, in addition to kinetic parameters, the catalytic life and stability of Cld are important considerations. Multiple investigators have found that Cld has a limited catalytic life, irreversibly inactivating after a limited number of turnovers (Stenklo et al., 2001; Streit and DuBois, 2008; Hofbauer et al., 2014a). Despite previous work with several Cld isozymes (Schaffner et al., 2015), to our knowledge the maximum turnover number has only been quantified for two Clds (Streit and DuBois, 2008; Celis et al., 2015). Catalytic inactivation of Cld is believed to be due to the occasional escape of a hypochlorite intermediate from the active site of the enzyme, resulting in irreversible oxidative damage (Hofbauer et al., 2014a). Furthermore, when the stability of perchlorate-reducing biocatalysts was examined under non-reactive conditions, chlorite was the first intermediate to accumulate, suggesting that Cld has the shorter shelf life of the two enzymes (Hutchison et al., 2013). These previous observations on catalytic inactivation and shelf life suggest that Cld would be the limiting component in biocatalytic treatment of perchlorate and chlorate, in addition to being the only biocatalyst required for chlorite removal.
We hypothesize that isozymes of Cld will vary in characteristics relevant for drinking water treatment. To investigate the potential for biocatalytic chlorite degradation, we characterized several Cld isozymes, in essence mining biology for the most suitable enzyme for removal of environmental contaminants. We assembled a library of seven Cld isozymes and quantified their performance under comparable conditions. We targeted three characteristics of Cld relevant to large-scale application: kinetic parameters in soluble protein fractions, catalytic inactivation, and shelf life. The results presented here demonstrate favorable activity and stability in soluble protein fractions as well as significant variation in catalytic life, affecting which Cld isozymes would be best suited for water treatment and other environmental applications.
Materials and Methods
Strains and Plasmids
Native and recombinant cld-expressing strains used in this work are described in Table 1. Recombinant plasmids were transferred by electroporation into Escherichia coli BL21 (DE3) using a MicroPulserTM Electroporator (BioRad, Hercules, CA, United States) and 0.1 cm electroporation cuvettes, following the manufacturer’s instructions. All the expression plasmids used in this work utilized the Bacteriophage T7 Promoter system.
Production of Soluble Protein Fractions Containing Cld
Native bacterial strains were grown on a modified mineral media as described (Hutchison et al., 2013), except that AlK(SO4)2-12H2O and H3BO3 were supplemented to a final concentration of 0.1 mg L-1 and yeast extract was omitted for M. bellicus VDY. Sodium chlorate was used as an electron acceptor instead of sodium perchlorate for all strains except A. oryzae PS, because of a prior report that Magnetospirillum bellicus VDY transiently accumulates chlorate when reducing perchlorate (Thrash et al., 2010). The headspace was 80% N2/20% CO2. Growth was carried out at 30°C with constant shaking at 150 rpm until the optical density at 600 nm (OD600) was between 0.5 and 0.6.
Plasmids were maintained by including ampicillin or carbenicillin to a final concentration of 50 μg mL-1. Production cultures of 500 mL were grown in Lennox Luria Broth media until the OD600 was approximately 1.0. At that time, hemin (Fisher Scientific, Hampton, NH, United States) was added to a final concentration of 0.5 mg mL-1. Expression was induced with 0.4 mM of isopropyl β-D-1-thiogalactopyranoside (Research Products International, Mount Prospect, IL, United States). Cultures were then allowed to express overnight (∼18 h) at 37°C with shaking at 175 rpm.
The methods to generate soluble protein fractions containing Cld were as previously described (Hutchison et al., 2013). In brief, cells were harvested by centrifugation, lysed by sonication, and fractionated by ultracentrifugation at 140,000 × g for 1 h at 4°C. After ultracentrifugation, the middle fraction (soluble protein fraction) was extracted using a glass pipette. Glycerol was added to a concentration of 10% v/v and aliquots were stored at -80°C.
Cloning and Purification of Cld
The cld gene was amplified from A. oryzae PS without a signal peptide using these primers: forward (5′-TCTGG ATCCGCAGCAGGCAATGCAACCC) and reverse (5′-GATGTCGACTTAATCGGCTAGCGCCTTG). The amplified product was cloned into E. coli BL21 (DE3) using SalI and BamHI (New England Biolabs, Ipswich, MA, United States) digests with standard molecular biology techniques (Sambrook and Russell, 2001). Protein expression and preparation of soluble protein fractions were as described in previous sections. Cld was purified from the soluble protein fraction using Strep-Tactin Sepharose (IBA, Göttingen, Germany) in a gravity flow column following the manufacturer’s instructions, without EDTA. Protein purification was confirmed with SDS–PAGE and Coomassie staining.
Cld Quantification Methods
Total protein was quantified with the bicinchoninic acid protein assay kit (Thermo Fisher Scientific, Waltham, MA, United States) in 96-well plates. After incubation, the absorbance at 526 nm was measured with a SpectraMAX 384 Plus Microplate Reader (Molecular Devices, Sunnyvale, CA, United States).
Total Heme Assay
Total heme was measured as an estimate of active Cld concentration using the pyridine hemochrome assay developed by Berry and Trumpower (1987). Aliquots of soluble protein fractions were oxidized in a buffer containing 20% pyridine, 100 mM NaOH, and 0.3 mM K3Fe(CN)6. After recording the absorbance spectrum, the solution was reduced by addition of 10 μL of freshly prepared sodium dithionite stock (0.5 mg μL-1) and mixed by inversion. The reduced spectrum was recorded twice. If there was a difference between the two reduced spectra, another 10 μL of dithionite was added to ensure the solution was completely reduced before recording the final spectrum. The heme concentration was calculated from the difference between the final reduced spectrum and the oxidized spectrum, applying the dual wavelength extinction coefficient of 24 mM-1 cm-1 at either 556 and 540 nm, for the recombinant Clds, or 550 and 535 nm, for the native Clds.
Cld Activity Assays
The kinetics of chlorite decomposition were monitored by quantifying product formation with an ion selective electrode (ISE) for chloride (Phoenix, Houston, TX, United States), similar to experiments in whole cells performed by Xu and Logan (2003). Data were collected at 0.5 s intervals with a National Instruments (Santa Clara, CA, United States) USB-6008 analog input module and a custom MATLAB data collection program. The probe was calibrated daily using a nine-point standard curve ranging from 1 to 1,000 ppm.
Reactions were carried out in 25 mL glass bottles that were continuously stirred at room temperature (21–23°C). The 10 mL reaction mixtures contained 0.0 to 5.0 mM sodium chlorite (Amresco, Solon, OH, United States) (prepared daily) in 10 mM phosphate buffer pH 7.0. Reactions were initiated by the addition of 10–20 μL of soluble protein fraction. As a control, the probe response to soluble protein fraction in the absence of chlorite was recorded. Typically the soluble protein fraction accounted for a response of 0.2 ppm or less. At least three independently grown and processed replicates were tested for each isozyme. The initial reaction rates were determined using a least squares fit to the linear portion of the reaction curve in OriginLab 9.1. Initial rates from at least 10 chlorite concentrations were then plotted against initial substrate concentration to generate a Michaelis–Menten plot. The maximum reaction velocity (Vmax) and half-saturation constant (Km) were determined by utilizing a least squares estimation of the data to the Michaelis–Menten equation (Hutchison and Zilles, 2015) in MATLAB. As a negative control for the recombinant Clds, the expression strain with an empty pET51b(+) plasmid was grown under similar conditions with and without the added hemin and assayed for Cld activity.
Catalytic inactivation of the Clds was quantified using two methods: activity decay and heme bleaching. In both cases, heme quantification was used as an estimate of Cld concentration in soluble protein fractions and results were reported using the maximum theoretical turnover number (MTTN). Cld isozymes were compared via one-way ANOVA analysis using Tukey’s pairwise comparison at a significance level of 95% in OriginLab 9.1. Activity decay was compared to heme bleaching with an unbalanced two-factor ANOVA (p < 0.05).
Catalytic inactivation was quantified with the activity decay method, as described by Streit and DuBois (2008). Soluble protein fractions were exposed to chlorite concentrations between 0 and 200 mM at room temperature until bubble formation ceased. Substrates and products were removed through three cycles of buffer exchange with a spin filter (Amicon, 10 kD Cutoff, EMD Millipore, Hayward, CA, United States). Following the final exchange, the solution volume was adjusted to match the original volume of the soluble protein fraction and the protein concentration was quantified. Activities were measured with the ISE chloride probe assay. An identically handled sample that was not exposed to chlorite served as the reference activity. The fraction of remaining activity was plotted against the molar ratio of chlorite to heme to determine the MTTN.
Catalytic inactivation was also quantified based on the extent of heme bleaching, by following a prominent Soret adsorption in the 400 nm range that is characteristic of porphyrins and other heme binding proteins (Streit and DuBois, 2008; Mayfield et al., 2013; Celis et al., 2015). Aliquots of soluble protein fraction (25 μL) were incubated with increasing concentrations of chlorite from a fresh 1.0 M stock solution. The total volume was adjusted to 1 mL with 10 mm phosphate buffer at pH 7.0. After the formation of bubbles ceased, the samples were briefly centrifuged to eliminate the bubbles, and their ultraviolet and visible spectra were recorded. The absorbance peak was calculated by manually subtracting a linear baseline, then the peak height was plotted against the number of turnovers per heme. Complete conversion of chlorite to chloride was assumed. Similarly to monitoring of activity decay, a line was fit to the initial linear region of the curve, and the x-intercept corresponded to the MTTN.
Shelf Life Experiments
The long-term stability of the various Clds was determined by tracking the decrease in Vmax of samples stored at 4 and at 22°C. Following glycerol addition, the soluble protein fraction was aliquoted into 1.5 mL microcentrifuge tubes and sealed with parafilm. For each timepoint, chlorite decomposition was measured at 1.5 and 3.0 mM sodium chlorite in duplicate from a single aliquot. Assays were conducted at room temperature, which typically fluctuated between 21 and 23°C, with one data point taken at 25°C. Sample activities were adjusted to relative activities at 22°C using the Arrhenius equation (Hutchison and Zilles, 2015). Changes in activity were normalized to the activities at 1.5 and 3.0 mM measured on day zero.
Data are reported as averages with standard deviation. ANOVA analysis was performed in OriginLab 9.1 with differences reported at a significance level of 95%. Cld isozymes were compared via one-way ANOVA analysis using Tukey’s pairwise comparison. Activity decay was compared to heme bleaching with an unbalanced two-factor ANOVA.
Kinetic parameters Km and Vmax were measured for soluble protein fractions containing each of the seven Cld isozymes and are given in Table 2. The most striking observation was that rNdCld has a relatively high Km. The remaining six Clds all had lower, and similar, values for Km. For comparison, purified rAoPS Cld had a Km of 180 μM. Attempts to quantify Cld in the soluble protein fractions using Western blots were unsuccessful due to different affinities for the isozymes. Throughout this work, Vmax values were therefore normalized to total heme rather than Cld concentration. This approach has been used previously to quantify active, purified Cld, accounting for incomplete incorporation of heme with an approximately 1:1 molar ratio of heme to active Cld protein (Streit and DuBois, 2008). In the current work, this approach also accounts for any differences in expression of Cld, assuming that non-Cld heme is either negligible or constant in the soluble protein fractions. Vmax values and catalytic efficiencies were relatively similar across the seven Clds (Table 2). The only statistically significant difference in catalytic efficiency was between rNwCld and MbCld. Using the same normalization method, purified rAoPS Cld had a Vmax of 7.2∗104 μmol min-1 μmolheme-1. Cld activity was below detection in the expression strain with an empty vector.
Two methods were used to quantify inactivation: activity decay and heme bleaching. Comparing the seven Cld isozymes with the activity decay method, rIdCld had an MTTN of 150,000, while the others had catalytic lifespans equal to or shorter than DaCld at 21,000 turnovers (Figure 1A). With this method, the only statistically significant difference in MTTN was between rIdCld and all the other Clds. The trends from the heme bleaching method were generally in agreement with the results from activity decay (Figure 1B). The rNwCld was not tested with this method due to poor expression. With the heme bleaching method, the rIdCld again had a significantly larger MTTN of 130,000, as compared to the other isozymes. rNdCld had the lowest MTTN of 11,000; this value was significantly lower than AoPSCld and MbCld as well as rIdCld.
FIGURE 1. Maximum theoretical turnover number. Comparison of maximum theoretical turnover calculated via activity decay (A) and heme bleaching (B). The average of three biological replicates is shown for each isozyme, with error bars showing standard deviation. Horizontal half circles denote significant difference (p < 0.05) in mean as compared with rIdCld. Vertical half circles denote significant difference (p < 0.05) as compared to rNdCld. rNwCld was not measured by the heme bleaching method because of poor expression.
A key concern for environmental applications is whether biocatalysts will have sufficient stability to be transported and stored in a cost-effective manner. The stability of selected Cld isozymes under non-reactive conditions, referred to here as shelf life, was therefore tested at 4 and 22°C. Specifically, rIdCld was tested due to its high MTTN, and AoPSCld was tested both in soluble protein fractions and in purified form. The activity was surprisingly stable (Figure 2). The soluble protein fractions had Cld activity even after 90–100 days.
FIGURE 2. Shelf life of Cld. Stability of stored chlorite dismutase, referred to as shelf life, is presented for (A) soluble protein fraction containing rIdCld, (B) soluble protein fraction from A. oryzae PS, and (C) purified, heterologously expressed Cld from A. oryzae PS. Storage temperatures were 4 (open squares) and 22°C (solid circles). The average decay in activity from three biological replicates over time was normalized to day zero activity at the specified storage temperature. Error bars represent standard deviation.
Three protein families share structural similarities within the peroxidase-chlorite superfamily. The families are Cld, Cld-like, and Dyp-type peroxidases. This work focused primarily on the Cld family, as the other families exhibit slower chlorite degradation (Zamocky et al., 2015). Seven Clds were tested, including two from species not known to reduce perchlorate or chlorate (Candidatus Nitrospira defluvii and Nitrobacter winogradskyi). An expression plasmid for one Cld-like protein, from Thermus thermophilus, was tested, but did not show good expression or detectable activity, so it was excluded from further analysis.
The kinetics observed here from soluble protein fractions showed a general trend of being slightly less favorable than published values for purified Cld. The Km values tended to be slightly higher, while the catalytic efficiencies (kcat/Km ratios) tended to be slightly lower. These differences are not due to our assay procedures, since the purified rAoPSCld showed good agreement with published values. Its Km was 180 μM, as compared to the published Km of 170 μM for AoGRCld, and its kcat was 930 s-1, as compared to the published kcat of 1,200 s-1, also for AoGRCld (van Ginkel et al., 1996). Differences between previously published values and those measured here could be due to the use of soluble protein fractions, as compared to purified proteins in previous work. For large-scale treatment applications, slight improvements in kinetic parameters for purified Clds would have to be weighed against the additional costs incurred by purification.
Comparing the two methods of measuring catalytic inactivation, the MTTNs found using the heme bleaching were significantly larger. Reasonable agreement was observed between the MTTN measured here for DaCld (21,000) and the previously reported value for purified rDaCld (17,000) (Streit and DuBois, 2008), and a similar discrepancy between the two methods was previously reported (Streit and DuBois, 2008; Celis et al., 2015). The most likely explanation is that the MTTNs measured by heme bleaching are artificially high due to the inability of this method to capture non-heme damage to Cld, since inactivation is known to occur through damage to both the heme moiety and the protein backbone (Hofbauer et al., 2014a). Two other possible explanations are specific to the conditions used in this study. One is that if non-Cld heme were less susceptible to damage, the presence of non-Cld heme in the soluble protein fractions could decrease the observed heme bleaching and therefore give a higher observed MTTN in the heme bleaching assay. The other is that the small reaction volume used here in the heme bleaching assays could have resulted in some product inhibition, slowing the reaction rate. This could have resulted in incomplete chlorite degradation and again given a higher observed MTTN. In these reactions, chloride concentrations reached up to 500 mM, which is higher than the estimated inhibitory constant (KI) of 225 mM (Streit and DuBois, 2008). However, the fact that similar discrepancies between the two methods were observed in two previous studies with purified Clds and larger reaction volumes (Streit and DuBois, 2008; Celis et al., 2015) suggests that most of the observed difference is due to non-heme damage.
The rNdCld had the lowest MTTN at 7,000 turnovers. For comparison, data from another study of NdCld can be used to estimate an MTTN of 5,000 turnovers (Hofbauer et al., 2014a). In combination with its relatively high Km, this low MTTN suggests that NdCld would be a poor candidate for biocatalytic water treatment. This conclusions run counter to other studies promoting NdCld as a promising candidate for biotechnology applications (Hofbauer et al., 2014b). However, those conclusions were based on the greater thermal and conformation stability of NdCld as compared to NwCld (Hofbauer et al., 2012), and did not consider the relatively high Km and low MTTN reported here for NdCld, which do not support its use in biocatalytic applications.
To understand the implications of these catalytic inactivation results for drinking water treatment applications, we examined two scenarios of chlorite contamination. The first scenario modeled a perchlorate treatment system as previously described (Hutchison and Zilles, 2015), with an influent concentration of 100 μg perchlorate L-1 and an effluent concentration of 10 μg perchlorate L-1. Based on the MTTN from activity decay and a Cld to total protein ratio of 0.25 ± 0.09, only 0.11% of the chlorite degradation capacity for the A. oryzae soluble protein fraction would be required under this scenario. A. oryzae soluble protein fraction was used for these calculations because it contains both perchlorate reductase and Cld.
The second scenario modeled applications requiring treatment of chlorite, where the influent and effluent chlorite concentrations are higher. This model was run for an influent of 5 mg L-1 (Michael et al., 1981) and an effluent concentration of 1 mg L-1, based on the United States Environmental Protection Agency’s Primary Drinking Water standard. In this second scenario, 7.4% of the chlorite degradation capacity was required. Alternatively, using soluble protein fraction with rIdCld and an expression ratio of 0.08 ± 0.01, the required chlorite decomposition only consumed 2.1% of Cld capacity. Catalytic inactivation of Cld is therefore unlikely to limit biocatalytic perchlorate or chlorite degradation. With development of an immobilized enzyme system, catalytic inactivation could become limiting in either scenario, but in that case the Cld dosage could be increased. It is also possible that the catalytic life of Cld could be extended further. Some mammalian peroxidases are protected from substrate-mediated inactivation through covalent linkages between the polypeptide and the porphyrin moiety (Wojciechowski et al., 2005; Jakopitsch et al., 2014). However, no Clds are known to or predicted to have this motif.
The shelf life experiments evaluate the potential storage of the biocatalysts before use. These results are especially notable considering that nothing was added to prevent growth or protease activity in these samples. The shelf life at 4°C was similar to a previous study on perchlorate reducing biocatalysts (Hutchison et al., 2013), while the 22°C shelf life observed here was longer. The discrepancy may be due to the use of temperature-controlled storage in this study. The purified rAoPSCld was the only one to completely lose activity during the test period. As the purified rAoPSCld lost activity more quickly than the same isozyme in the soluble protein fraction, we hypothesize that the soluble protein fraction contains other compounds that are responsible for the increased shelf life.
Overall, Cld from Ideonella dechloratans exhibited the best properties for water treatment applications: low Km, high Vmax, low susceptibility to catalytic inactivation, and a long shelf life. Based on the turnover numbers observed here, catalytic inactivation could become an important design consideration if the biocatalysts were immobilized for reuse in perchlorate or chlorite removal. Continuing to identify or develop Clds with greater resistance to inactivation would therefore aid in development of this biocatalytic technology. Overall, this work supports the feasibility of biocatalytic degradation of environmental contaminants such as chlorite and perchlorate.
KM, JH, and JZ contributed to the conception and design of the work and production and revision of the manuscript. KM and JH collected and interpreted data. All authors read and approved the final submission.
This work was supported by the US National Science Foundation (CBET1336620), the University of Illinois at Urbana–Champaign University Fellowship (KM), the National Science Foundation Graduate Research Fellowship Program (DGE1144245) (JH) and the ARCS® (Achievement Rewards for College Scientists) Foundation, Inc.’s Scholar Illinois Chapter (JH).
Conflict of Interest Statement
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
The authors thank David Anderson for assistance with data collection. They thank Dr. Holger Daims at the University of Vienna and Drs. Maria Rova and Thomas Nilsson at Karlstad University for providing expression plasmids used in this work.
Berry, E. A., and Trumpower, B. L. (1987). Simultaneous determination of hemes a, b, and c from pyridine hemochrome spectra. Anal. Biochem. 161, 1–15. doi: 10.1016/0003-2697(87)90643-9
Celis, A. I., Geeraerts, Z., Ngmenterebo, D., Machovina, M. M., Kurker, R. C., Rajakumar, K., et al. (2015). A dimeric chlorite dismutase exhibits O2-generating activity and acts as a chlorite antioxidant in Klebsiella pneumoniae MGH 78578. Biochemistry 54, 434–446. doi: 10.1021/bi501184c
Chen, Y., Stemple, B., Kumar, M., and Wei, N. (2016). Cell surface display fungal laccase as a renewable biocatalyst for degradation of persistent micropollutants bisphenol A and sulfamethoxazole. Environ. Sci. Technol. 50, 8799–8808. doi: 10.1021/acs.est.6b01641
Danielsson Thorell, H., Beyer, N. H., Heegaard, N. H., Ohman, M., and Nilsson, T. (2004). Comparison of native and recombinant chlorite dismutase from Ideonella dechloratans. Eur. J. Biochem. 271, 3539–3546. doi: 10.1111/j.0014-2956.2004.04290.x
Ebihara, A., Okamoto, A., Kousumi, Y., Yamamoto, H., Masui, R., Ueyama, N., et al. (2005). Structure-based functional identification of a novel heme-binding protein from Thermus thermophilus HB8. J. Struct. Funct. Genomics 6, 21–32. doi: 10.1007/s10969-005-1103-x
Hofbauer, S., Gruber, C., Pirker, K. F., Sundermann, A., Schaffner, I., Jakopitsch, C., et al. (2014a). Transiently produced hypochlorite is responsible for the irreversible inhibition of chlorite dismutase. Biochemistry 53, 3145–3157. doi: 10.1021/bi500401k
Hofbauer, S., Gysel, K., Mlynek, G., Kostan, J., Hagmuller, A., Daims, H., et al. (2012). Impact of subunit and oligomeric structure on the thermal and conformational stability of chlorite dismutases. Biochim. Biophys. Acta 1824, 1031–1038. doi: 10.1016/j.bbapap.2012.05.012
Hofbauer, S., Schaffner, I., Furtmuller, P. G., and Obinger, C. (2014b). Chlorite dismutases - a heme enzyme family for use in bioremediation and generation of molecular oxygen. Biotechnol. J. 9, 461–473. doi: 10.1002/biot.201300210
Hutchison, J. M., Guest, J. S., and Zilles, J. L. (2017). Evaluating the development of biocatalytic technology for the targeted removal of perchlorate from drinking water. Environ. Sci. Technol. 51, 7178–7186. doi: 10.1021/acs.est.7b00831
Hutchison, J. M., Poust, S. K., Kumar, M., Cropek, D. M., MacAllister, I. E., Arnett, C. M., et al. (2013). Perchlorate reduction using free and encapsulated Azospira oryzae enzymes. Environ. Sci. Technol. 47, 9934–9941. doi: 10.1021/es402081b
Hutchison, J. M., and Zilles, J. L. (2015). Biocatalytic perchlorate reduction: kinetics and effects of groundwater characteristics. Environ. Sci.1, 913–921. doi: 10.1039/c5ew00176e
Jakopitsch, C., Pirker, K. F., Flemmig, J., Hofbauer, S., Schlorke, D., Furtmuller, P. G., et al. (2014). Mechanism of reaction of chlorite with mammalian heme peroxidases. J. Inorg. Biochem. 135, 10–19. doi: 10.1016/j.jinorgbio.2014.02.010
Karich, A., Ullrich, R., Scheibner, K., and Hofrichter, M. (2017). Fungal unspecific peroxygenases oxidize the majority of organic EPA priority pollutants. Front. Microbiol. 8:1463. doi: 10.3389/fmicb.2017.01463
Kostan, J., Sjoblom, B., Maixner, F., Mlynek, G., Furtmuller, P. G., Obinger, C., et al. (2010). Structural and functional characterisation of the chlorite dismutase from the nitrite-oxidizing bacterium “Candidatus Nitrospira defluvii”: identification of a catalytically important amino acid residue. J. Struct. Biol. 172, 331–342. doi: 10.1016/j.jsb.2010.06.014
Maixner, F., Wagner, M., Lucker, S., Pelletier, E., Schmitz-Esser, S., Hace, K., et al. (2008). Environmental genomics reveals a functional chlorite dismutase in the nitrite-oxidizing bacterium “Candidatus Nitrospira defluvii”. Environ. Microbiol. 10, 3043–3056. doi: 10.1111/j.1462-2920.2008.01646.x
Martínez, A. T., Ruiz-Dueñas, F. J., Camarero, S., Serrano, A., Linde, D., Lund, H., et al. (2017). Oxidoreductases on their way to industrial biotransformations. Biotechnol. Adv. 35, 815–831. doi: 10.1016/j.biotechadv.2017.06.003
Mayfield, J. A., Hammer, N. D., Kurker, R. C., Chen, T. K., Ojha, S., Skaar, E. P., et al. (2013). The chlorite dismutase (HemQ) from Staphylococcus aureus has a redox-sensitive heme and is associated with the small colony variant phenotype. J. Biol. Chem. 288, 23488–23504. doi: 10.1074/jbc.M112.442335
Michael, G. E., Miday, R. K., Bercz, J. P., Miller, R. G., Greathouse, D. G., Kraemer, D. F., et al. (1981). Chlorine dioxide water disinfection: a prospective epidemiology study. Arch. Environ. Health 36, 20–27. doi: 10.1080/00039896.1981.10667601
Mlynek, G., Sjoblom, B., Kostan, J., Fureder, S., Maixner, F., Gysel, K., et al. (2011). Unexpected diversity of chlorite dismutases: a catalytically efficient dimeric enzyme from Nitrobacter winogradskyi. J. Bacteriol. 193, 2408–2417. doi: 10.1128/JB.01262-10
Richardson, S. D., and Postigo, C. (2012). “Drinking water disinfection byproducts,” in Handbook of Environmental Chemistry, ed. D. Barceló (Berlin: Springer-Verlag), 93–138.
Sambrook, J., and Russell, D. W. (2001). Molecular Cloning: A Laboratory Manual. Cold Spring Harbor, NY: Cold Spring Harbor Laboratory Press.
Schaffner, I., Hofbauer, S., Krutzler, M., Pirker, K. F., Furtmuller, P. G., and Obinger, C. (2015). Mechanism of chlorite degradation to chloride and dioxygen by the enzyme chlorite dismutase. Arch. Biochem. Biophys. 574, 18–26. doi: 10.1016/j.abb.2015.02.031
Stenklo, K., Thorell, H. D., Bergius, H., Aasa, R., and Nilsson, T. (2001). Chlorite dismutase from Ideonella dechloratans. J. Biol. Inorg. Chem. 6, 601–607. doi: 10.1007/s007750100237
Streit, B. R., and DuBois, J. L. (2008). Chemical and steady-state kinetic analyses of a heterologously expressed heme dependent chlorite dismutase. Biochemistry 47, 5271–5280. doi: 10.1021/bi800163x
Thrash, J. C., Ahmadi, S., Torok, T., and Coates, J. D. (2010). Magnetospirillum bellicus sp. nov., a novel dissimilatory perchlorate-reducing alphaproteobacterium isolated from a bioelectrical reactor. Appl. Environ. Microbiol. 76, 4730–4737. doi: 10.1128/AEM.00015-10
van Ginkel, C. G., Rikken, G. B., Kroon, A. G. M., and Kengen, S. W. M. (1996). Purification and characterization of chlorite dismutase: a novel oxygen-generating enzyme. Arch. Microbiol. 166, 321–326. doi: 10.1007/s002030050390
Wojciechowski, G., Huang, L., and Ortiz de Montellano, P. R. (2005). Autocatalytic modification of the prosthetic heme of horseradish but not lactoperoxidase by thiocyanate oxidation products. A role for heme-protein covalent cross-linking. J. Am. Chem. Soc. 127, 15871–15879. doi: 10.1021/ja054084t
World Health Organization (2005). Chlorite and Chlorate in Drinking-Water. Geneva: World Health Organization.
Xu, J. L., and Logan, B. E. (2003). Measurement of chlorite dismutase activities in perchlorate respiring bacteria. J. Microbiol. Methods 54, 239–247. doi: 10.1016/S0167-7012(03)00058-7
Yang, J., Lin, Y., Yang, X., Ng, T. B., Ye, X., and Lin, J. (2017). Degradation of tetracycline by immobilized laccase and the proposed transformation pathway. J. Hazard. Mater. 322(Pt B), 525–531. doi: 10.1016/j.jhazmat.2016.10.019
Zamocky, M., Hofbauer, S., Schaffner, I., Gasselhuber, B., Nicolussi, A., Soudi, M., et al. (2015). Independent evolution of four heme peroxidase superfamilies. Arch. Biochem. Biophys. 574, 108–119. doi: 10.1016/j.abb.2014.12.025
Keywords: biocatalyst, catalytic inactivation, chlorite, drinking water, perchlorate
Citation: Mobilia KC, Hutchison JM and Zilles JL (2017) Characterizing Isozymes of Chlorite Dismutase for Water Treatment. Front. Microbiol. 8:2423. doi: 10.3389/fmicb.2017.02423
Received: 25 August 2017; Accepted: 22 November 2017;
Published: 12 December 2017.
Edited by:Michael Benedik, Texas A&M University, United States
Reviewed by:Yonghong Bi, Institute of Hydrobiology (CAS), China
Boonfei Tan, Singapore-MIT Alliance for Research and Technology, Singapore
Copyright © 2017 Mobilia, Hutchison and Zilles. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) or licensor are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Julie L. Zilles, email@example.com