Biochar, a charcoal-like product of the incomplete combustion of organic materials, is an increasingly popular soil amendment designed to improve soil fertility. We investigated the possibility that biochar could promote direct interspecies electron transfer (DIET) in a manner similar to that previously reported for granular activated carbon (GAC). Although the biochars investigated were 1000 times less conductive than GAC, they stimulated DIET in co-cultures of Geobacter metallireducens with Geobacter sulfurreducens or Methanosarcina barkeri in which ethanol was the electron donor. Cells were attached to the biochar, yet not in close contact, suggesting that electrons were likely conducted through the biochar, rather than biological electrical connections. The finding that biochar can stimulate DIET may be an important consideration when amending soils with biochar and can help explain why biochar may enhance methane production from organic wastes under anaerobic conditions.
Biochar, which is produced by heating biomass in a closed system with limited oxygen supply, has been promoted as an amendment to improve soil quality1,2, but the impact of biochar on soil microbial communities is poorly understood. Biochar has been used to enhance soil fertility3, remediate pollution, decrease green house gas emissions4 and sequester carbon in a worldwide quest to achieve carbon neutrality4. Biochar is hypothesized to increase the microbial soil content by concentrating organic substrates and nutrients on its surface5. Another feature of biochar that could potentially influence the activity of soil microbiota is that biochar is electrically conductive6. Conductive minerals/materials such as magnetite or GAC facilitated DIET by accelerating rates of anaerobic metabolism7,8,9,10. Under certain conditions, DIET is considered to be potentially more effective for interspecies electron transfer than strategies such as interspecies H2 or formate transfer that rely on the diffusion of electron carriers between species11,12.
DIET has been shown possible in the absence of conductive materials via biological electrical connections such as pili13,14,15,16,17. For example, Geobacter metallireducens and Geobacter sulfurreducens grew in co-culture via DIET in a medium with ethanol as the electron donor and fumarate as the electron acceptor13. The two organisms needed to cooperate in order to metabolize ethanol and grow, because G. metallireducens can utilize ethanol as an electron donor, but is unable to use fumarate as an electron acceptor18, whereas G. sulfurreducens cannot use ethanol as an electron donor, but can reduce the electron acceptor, fumarate19. In co-culture, G. metallireducens produced acetate from ethanol and G. sulfurreducens utilized the electrons released from the ethanol oxidation as well as the acetate produced for fumarate reduction13. Multiple lines of evidence13,14,15,16,17 demonstrated that interspecies electron transfer in Geobacter co-cultures proceeded via DIET rather than H2 or formate transfer and that the Geobacter pili, which posses metallic-like conductivity20,21, were required during DIET.
However, the initial adaption of Geobacter co-cultures to interspecies electron transfer via pili-mediated DIET took ca. 30 days13. GAC substantially reduced the adaptation period for growth via DIET, with ethanol metabolism evident within a day9. Furthermore, the mechanism for DIET in the presence of GAC appeared to be different because strains of G. sulfurreducens deficient in pili or the pili-associated cytochrome OmcS, were incapable of DIET in the absence of GAC13, but functioned as well as wild-type in the presence of GAC9. Instead of forming close cell-to-cell connections as observed in the absence of GAC13, both species attached to the electrically conductive GAC suggesting that GAC served as a cell-to-cell conduit for electron flow between electron-donating and electron-accepting cells. GAC also accelerated electron transfer between G. metallireducens and M. barkeri promoting methane production from ethanol and enhanced methane production was observed if aggregates from an anaerobic wastewater digester were amended with GAC9.
Biochar, is a GAC precursor22 and chemical or physical activation of biochar yields GAC, with a higher surface area, porosity and increased aromaticity23,24. Electron conduction through a solid conductive medium is substantially different than molecular diffusion of shuttles. Conduction through solid materials involves migration of electrons in response to a difference in voltage potential whereas concentration gradients drive diffusion of shuttles. The term electron shuttle typically refers to soluble molecules such as humic substances25, cysteine26, redox active metals27, or flavins28 that can accept electrons from one microorganism and donate them to another electron acceptor29 as a result of concentration gradients.
In this study we addressed the impact of biochar on syntrophic associations based on DIET. Syntrophic associations are at the root of carbon cycle in the environment and this report unravels biochar as a potential contributor to methane emissions in the environment. We report on studies on the impact of biochar in defined co-cultures with G. metallireducens, an effective microorganism for evaluating DIET because it can donate electrons via DIET and not by interspecies H2 or formate transfer13,14,16,18.
Biochar stimulates DIET in Geobacter co-cultures
The addition of biochar to co-cultures of G. metallireducens and G. sulfurreducens in medium with ethanol as the electron donor and fumarate as the electron acceptor stimulated syntrophic metabolism of ethanol (Figure 1A) with the reduction of fumarate to succinate (Figure 1B) within two days. In contrast, a control co-culture of G. metallireducens and G. sulfurreducens, not amended with biochar, required ca. 30 days to adapt to ethanol metabolism13. Rates of ethanol loss and succinate production with a water-soluble extract of the biochar were only slightly faster than the biochar-free control (Figure 1), suggesting that the particulate fraction of the biochar was primarily responsible for stimulating co-culture metabolism.
The rates of ethanol metabolism varied somewhat with the biochar types, but this could not be correlated with the small differences in conductivity because the co-cultures amended with ESI biochar, which had the lowest conductivity (Table 1), metabolized ethanol at rates intermediate between the BEC and Kiln biochars, which both had conductivities ca. 2-fold higher. The fast rates of ethanol metabolism in the presence of biochar were comparable with those previously observed with the same quantity of GAC9. However, the conductivity of GAC (3000 ± 327 μS/cm) measured with the same method9 was substantially higher than that of biochar (Table 1). On the other hand, a non-conductive material, glass beads, did not promote DIET under similar conditions9. In co-cultures amended with biochar acetate did not accumulate and thus the oxidation of each mole of ethanol to carbon dioxide was coupled to the reduction of fumarate, the electron acceptor for G. sulfurreducens and was expected to result in the production of six moles of succinate (reaction 1).
C2H6O + 6 C4H4O4 + 3 H2O → 2 CO2 + 6 C4H6O4 (reaction 1)
The amounts of ethanol consumed and succinate produced in the 10 days of incubation (mean ± standard deviation; n = 3) in the presence of the BEC, ESI and Kiln biochars were 8.10 ± 0.72/34.98 ± 0.48; 6.98 ± 0.47/33.37 ± 0.24; and 5.15 ± 0.23/30.81 ± 1.28, respectively. Thus, the reduction of fumarate to succinate accounted for 72–88% of the electrons, which were derived from the ethanol removal in the biochar-amended cultures. In co-cultures amended with biochar, most (78%) of the co-culture protein was firmly attached to the solid particles of biochar, after 10 days of incubation (Figure 2A). Quantitative PCR analysis of the attached cells indicated that the majority (69%) were G.sulfurreducens (Figure 2B). Scanning electron microscopy revealed that attached cells did not form aggregates (Figure 3) like co-cultures without biochar, suggesting that direct biological connections between the cells were unnecessary.
Cultures comprised solely of G. metallireducens slowly metabolized ethanol with a corresponding increase in acetate (Figure 4A), suggesting that biochar served as an electron acceptor (reaction 3).
C2H6O + H2O + (Biocharox.) → C2H4O2 + 4H+ + 4 e− (Biocharred.) (reaction 2)
There was no ethanol metabolism in the absence of biochar (Figure 4B).
From the amount of ethanol metabolized over 10 days (2.8 mmol/L × 0.01 L = 0.028 mmol) and the stoichiometry of electron release from ethanol metabolism to acetate (4 mmol electrons/mmol ethanol) it can be estimated that the 0.25 g of biochar in the culture tubes accepted 0.112 mmoles of electrons from G. metallireducens, which is ca. 0.5 mmoles of electrons accepted per gram of biochar. This is comparable to 0.35 mmoles of electrons that a gram of soil humic substances is capable of accepting during microbial reduction processes30. However, unlike humic substances that, once reduced, can donate electrons to Fe(III)25,31, no Fe(III) was reduced when the reduced biochar was exposed to Fe(III) citrate, suggesting that, as previously demonstrated for GAC9, electron transport through biochar is unlikely to be attributed to quinone moieties, but rather to the conductive properties of the materials. Our Fe(III) citrate experiments with bioreduced biochar were carried out under physiological conditions (pH 6.5–7.0) unlike a previous study which reported that reduced activated carbon37 could reduce Fe(III) citrate at low pH conditions37.
Biochar stimulation of DIET in methanogenic co-cultures
Some methanogenic communities may exchange electrons via DIET16,32. DIET was recently confirmed in co-culture studies with G. metallireducens and Methanosaeta harundinacea16, a study which also demonstrated that G. metallireducens was unable to produce H2 or formate to provide electrons for CO2 reduction to methane by H2/formate utilizing methanogenic partners like Methanospirillum hungatei or Methanobacterium formicicum16. The impact of conductive materials on DIET and methanogenesis in defined systems was apparent from studies with co-cultures of G. metallireducens and M. barkeri amended with GAC9. Amending co-cultures of G. metallireducens and M. barkeri with biochar stimulated the conversion of ethanol to methane (Figure 5A). There was a transient accumulation of acetate, but methane production was dependent on ethanol metabolism following reaction 2.
2 CH3CH2OH → 3 CH4 + CO2 (reaction 3)
In the presence of biochar the metabolism of 21 ± 1 mM ethanol (i.e. 210 μmol in 10 ml media) yielded 16 ± 2 mmol/l methane (i.e. 272 μmol in 17 ml headspace). Thus, 86% of the electrons from ethanol metabolism were recovered in methane. In contrast, there was no ethanol metabolism or methane production in the G. metallireducens-M. barkeri co-cultures in the absence of biochar (Figure 5B) or with M. barkeri alone in the presence of biochar (Figure 5C). The water-soluble biochar fraction had only a minor stimulatory impact on ethanol metabolism in the G. metallireducens-M. barkeri co-cultures, suggesting that the solid phase was the primary stimulatory component (Figure 5D).
Similar to Geobacter co-cultures, most of the cell protein (71%) was firmly associated to the biochar particles in the methanogenic co-culture (Figure 6A) and 87% of the attached cells were G. metallireducens (Figure 6B). The higher abundance of G. metallireducens in the co-culture with M. barkeri, compared with the co-culture with G. sulfurreducens may be due to larger bio-volume of M. barkeri versus G. sulfurreducens, as apparent from SEM micrographs (Figure 3, 7), as well as the lower energy yield from methane production versus fumarate reduction. Scanning electron microscopy revealed that G. metallireducens and M. barkeri attached to the biochar, but did not form aggregates with each other, suggesting that the electrical connections between the two species were through the biochar rather than via cell-to-cell electron transfer (Figure 7).
The results demonstrate that biochar has sufficient conductivity to promote direct electron transfer between syntrophic partners in co-cultures based on DIET. This provides a potential explanation for observations that some biochar amendments can enhance methane production in soils33 or in small-scale digesters converting organic waste to methane34,35.
The results suggest that biochar promotes interspecies electron exchange via a conduction-based mechanism, in which electrons migrate through the biochar from electron-donating to electron-accepting cells. This is similar to the mechanism proposed for interspecies electron transfer through GAC9, but differs significantly from extracellular electron exchange with electron shuttles such as humic substances25. In the absence of conductive materials, microorganisms growing together, required a long adaption time and numerous transfers13, to get to the same substrate consumption rates as those observed with biochar or GAC9. This suggests that cells required time to express cellular components required for extracellular electron transfer14.
The ability of biochar to promote DIET with similar rates and stoichiometries as those observed in co-cultures amended with GAC9, might be surprising considering the conductivity of biochar is 1000-fold less than that of GAC. The higher conductivity of activated carbon is likely due to increased surface area and porosity and increased aromatization, which happens during the conversion of biochars into activated carbon at higher temperatures22,23. Aromaticity, a consequence of electron delocalization between aromatic rings localized on distinct neighboring planes, gives conductive properties to graphite, charcoals or other organic polymers24 and as discovered recently even to the pili of Geobacter species21. The conductivity of the biochars evaluated here was comparable to that of G. sulfurreducens pili preparations20,21,which are sufficient to effectively promote DIET. The ability of biochar to stimulate DIET appears to overcome the adaption period that cells require to begin expressing high levels of the components that are required for pili-based DIET13,14,16. Materials with increased aromaticity are doped by reduction or oxidation reactions36. If the acceptor microorganism reduces sections of the biochar and the donor microorganism oxidizes sections of the biochar, there will be intrinsic charge differences between sections of biochar, promoting electron flow. This has been also noted on activated carbon, which accepted electrons from microorganisms and then released the electrons to Fe(III) citrate under acidic conditions38.
However, biochar is a complex material and can modify environments to which it is added with properties other than conductivity. For example, biochar was speculated to act as a “shuttle” to mitigate N2O emissions during denitrification in soils38. Whereas other studies suggested that N2O formation in soils is due to abiotic processes happening on biochars surface enriched in surface charged groups, like quinones, metal ions or radicals39,40.
Our observations that biochar increases methane production in defined co-culture systems, in which partners were capable of direct electron transfer, changes the present understanding that biochar could mitigate methane gas emissions. Considering the potential significant impact of methane production on global warming and the persistence of biochar in soil, warrants further long-term studies on how soil methanogenic communities are affected by biochar amendments and the impact of biochar on the global carbon cycle.
Characterization of biochars
Three pine biochars that differed somewhat in their mode of production, particle size and surface area were evaluated (Table 1). All biochars were sieved (pore size 3 mm) and the size of particles was inspected with a transmission electron microscope. The Brunauer-Emmett-Teller (BET) surface areas of the other three kinds of biochar were calculated from the N2 adsorption and desorption isotherms at 77°K obtained using Quantachrome Autosorb-1 as previously described41. The electrical conductivities of biochar were determined by two-probe electrical conductance measurements using two gold electrodes separated by 50 μm non-conductive gap, as previously described13,20. Biochar was placed between the two gold electrodes to bridge the non-conductive gap. Voltage was applied using a Keithley 2400 sourcemeter. Voltage was scanned from 0 V to +0.05 V in steps of 0.025 V. For each sample, current was measured 100 seconds after setting the voltage to allow the exponential decay of the transient ionic current in the gap and to measure steady state electronic current42. We collected data with the Labview data acquisition system (National Instruments, TX, USA) and data analyses were performed with Igor Pro (Wavemetrics Inc., OR USA).
Microorganisms, media and growth conditions
Geobacter metallireducens strain GS-15 (ATCC 53774), Geobacter sulfurreducens strain PCA (ATCC 51573) and Methanosarcina barkeri type strain, DSM 800 (ATCC 43569) were obtained from our laboratory culture collection. Prior to initiating the co-cultures, G. metallireducens was maintained in a medium with ethanol (10 mM) as the electron donor and Fe(III) citrate (55 mM) as the electron acceptor as previously described17. G. sulfurreducens was cultured routinely with 10 mM acetate as electron donor and 40 mM fumarate as electron acceptor in a fresh water mineral medium as previously described17. M. barkeri was maintained on DSMZ methanogenic medium 120 with 30 mM acetate as methanogenic substrate9. All pure cultures and co-cultures were incubated anaerobically, in 27 mL pressure tubes with 10 mL medium under an anoxic atmosphere of 80:20 of N2:CO2 as previously described13,17.
Co-cultures of G. metallireducens and G. sulfurreducens were initiated as previously described9,17 by introducing a 5% inocula of each microorganism into a medium with ethanol (10 mM) as the electron donor and fumarate (40 mM) as the electron acceptor. The incubation temperature was 30°C. Co-cultures of G. metallireducens and M. barkeri were initiated with a 5% inocula of each microorganism into DSMZ methanogenic medium 120 with 20 mM ethanol as the electron donor9. Incubations of the methanogenic cocultures were done at 37°C. All experiments were carried on with three biological replicates.
In order to test the effect of biochar amendments, 0.25 g of biochar was added to 0.5 ml of the appropriate co-culture medium, under N2:CO2 and the medium was autoclaved for 30 minutes. Additional sterile medium (9 ml) was added under anaerobic conditions, while ethanol and cells were inoculated afterwards.
Water extracts of biochar were obtained by incubating 0.25 g of biochar in 9 ml of culture medium on a shaker under sterile, anaerobic conditions for either 10 days (G. metallireducens - G. sulfurreducens co-cultures) or 20 days (G. metallireducens - M. barkeri co-cultures) to replicate the length of time that the co-cultures were exposed to biochar. Ethanol and cells were added afterwards.
Quantitative PCR analysis
DNA was extracted from the cells attached to biochar from triplicate 10 ml co-cultures as previously described9. To determine the specific abundance of cells in co-cultures amended with biochar, quantitative PCR was performed using G. metallireducens specific primers (Gmet_F 5′-TGGCCCACATCTTCATCTC-3′, Gmet_R 5′-TGCATGTTTTCATCCACGAT-3′), versus primers universal to both G. sulfurreducens and G. metallireducens (Geo16S_F 5′-GAGGTACCGTCAAGACCAA-3′, Geo16S_R 5′-GCCACACTGGAACTGAGACA-3′), or specific for Methanosarcina species (MB16S_F 5′- GGGTCTAAAGGGTCCGTAGC-3′, MB16S_R 5′ GTTCTGGTAAGACGCCTTCG-3′), depending on the type of co-culture tested. Before conducting the quantitative PCR experiment primer pairs were validated for the primer efficiency. The quantitative PCR was carried out using Fast Syber green master mix (ABI) in Real time PCR cycler (ABI-9500) following the manufacturer's protocol.
Scanning electron microscopy
In order to evaluate cell attachment to biochar, the biochar-attached fraction was studied by scanning electron microscopy at the end of the co-culture growth (day 10 of the G. metallireducens-G.sulfurreducens cycle and day 20 of the G. metallireducens-M. barkeri). Samples were first fixed with 2.5% glutaraldehyde in 0.1 M phosphate buffer for up to 12 hours at 4°C, then washed 3 times in 0.1 M phosphate buffer at 4°C for 10 min each, dehydrated further in an ethanol/water mixture of 50%, 70%, 80%, 90%, 95% and 100% for 10 minutes each (dehydration in 100% ethanol was done 3 times) and at last immersed twice for 30 seconds in pure hexamethyldisilazane (Sigma Aldrich, St Louis, MO, USA) followed by 10 minutes of air-drying43.
Subsamples for gas chromatographic analysis of methane and ethanol and high performance liquid chromatography analysis of acetate, fumarate, formate and succinate were withdrawn and processed as previously described32. In order to further support biomass attachment onto biochar at the end of co-culture incubations, the liquid fraction was separated from the biochar by lysis of the biochar in 0.5 N NaOH and bead beating for 30 seconds with sterile glass beads to ensure cell disruption. Cell protein in the culture supernatant and biochar fractions was determined using the bicinchoninic acid method44 with bovine serum albumin (BSA) as protein standard.
Lehmann, J. A handful of carbon. Nature 447, 143–144 (2007).
Zheng, H. et al. Characteristics and nutrient values of biochars produced from giant reed at different temperatures. Bioresour. Technol. 130, 463–471 (2013).
Chan, K., Van Zwieten, L., Meszaros, I., Downie, A. & Joseph, S. Using poultry litter biochars as soil ammendments. Soil Res. 46, 437–444 (2008).
Woolf, D., Amonette, J. E., Street-Perrott, F. A., Lehmann, J. & Joseph, S. Sustainable biochar to mitigate global climate change. Nat. Commun. 1, 56 (2010).
Lehmann, J. et al. Biochar effects on soil biota: A review. Soil Biol. Biochem. 43, 1812–1836 (2011).
Xu, W., Pignatello, J. & Mitch, W. Role of black carbon electrical conductivity in mediating hexahydro-1,3,5-triazine (RDX) transformation on carbon surfaces by sulfides. Environ. Sci. Technol. 34, 2472–2478 (2013).
Kato, S., Hashimoto, K. & Watanabe, K. Methanogenesis facilitated by electric syntrophy via (semi)conductive iron-oxide minerals. Environ. Microbiol. 14, 1646–1654 (2012).
Kato, S., Hashimoto, K. & Watanabe, K. Microbial interspecies electron transfer via electric currents through conductive minerals. Proc. Natl. Acad. Sci. USA 109, 10042–10046 (2012).
Liu, F. et al. Promoting direct interspecies electron transfer with activated carbon. Energy Environ. Sci. 5, 8982–8989 (2012).
Liu, F. et al. Magnetite compensates for the lack of a pilin-associated c-type cytochrome in extracellular electron transfer. Environ. Microbiol. 10.1111/1462-2920.12485. (2014).
Lovley, D. R. Live wires: direct extracellular electron exchange for bioenergy and the bioremediation of energy-related contamination. Energy Environ. Sci. 4, 4896–4906 (2011).
Lovley, D. R. Electromicrobiology. Annu. Rev. Microbiol. 66, 391–409 (2012).
Summers, Z. M. et al. Direct exchange of electrons within aggregates of an evolved syntrophic coculture of anaerobic bacteria. Science 330, 1413–1415 (2010).
Shrestha, P. M. et al. Transcriptomic and genetic analysis of direct interspecies electron transfer. Appl. Environ. Microbiol. 79, 2397–2404 (2013).
Shrestha, P. M. et al. Syntrophic growth with direct electron transfer as the sole mechanism for for energy exchange. Environ. Microbiol. Rep. 5, 904–910 (2013).
Rotaru, A. E. et al. A new model for electron flow during anaerobic digestion: direct interspecies electron transfer to Methanosaeta for the reduction of carbon dioxide to methane. Energy Environ. Sci. 7, 408–415 (2014).
Rotaru, A. E. et al. Interspecies electron transfer via hydrogen and formate rather than direct electrical connections in co-cultures of Pelobacter carbinolicus and Geobacter sulfurreducens. Appl. Environ. Microbiol. 78, 7645–7651 (2012).
Lovley, D. R. et al. Geobacter metallireducens gen. nov. sp. nov., a microorganism capable of coupling the complete oxidation of organic compounds to the reduction of iron and other metals. Arch. Microbiol. 159, 336–344 (1993).
Caccavo, F., Jr et al. Geobacter metallireducens sp. nov., a hydrogen- and acetate-oxidizing dissimilatory metal-reducing microorganism. Appl. Environ. Microbiol. 60, 3752–3759 (1994).
Malvankar, N. S. et al. Tunable metallic-like conductivity in microbial nanowire networks. Nat. Nanotechnol. 6, 573–579 (2011).
Vargas, M. et al. Aromatic amino acids required for pili conductivity and long-range extracellular electron transport in Geobacter sulfurreducens. mBio 4, e00105–13 (2013).
Azargohar, R. & Dalai, A. in 27th Symposium on Biotechnology for Fuels and Chemicals, Vol. 129–132. (eds. McMillan, J., Adney, W., Mielenz, J. & Klasson, K.) 762–773 (Humana Press, DenverCOUSA; 2006).
Lehmann, J. & Joseph, S. (eds.) Biochar for environmental management: science and technology. (Earthscan, London, Sterling, VA; 2009).
Bourke, J. et al. Do all carbonized charcoals have the same chemical structure? 2. A model of the chemical structure of carbonized charcoal. Ind. Eng. Chem. Res. 46, 5954–5967 (2007).
Lovley, D. R., Coates, J. D., Blunt-Harris, E. L., Phillips, E. J. & Woodward, J. C. Humic substances as electron acceptors for microbial respiration. Nature 382, 445–448 (1996).
Kaden, J., Galushko, A. & Schink, B. Cysteine-mediated electron transfer in syntrophic acetate oxidation by cocultures of Geobacter sulfurreducens and Wolinella succinogenes. Arch. Microbiol. 178, 53–58 (2002).
Nevin, K. P. & Lovley, D. R. Potential for nonenzymatic reduction of Fe (III) via electron shuttling in subsurface sediments. Environ. Sci. Technol. 34, 2472–2478 (2000).
Hernandez, M. & Newman, D. Extracellular electron transfer. Cell. Mol. Life Sci. 58, 1562–1571 (2001).
Lovley, D. R. Bug juice: harvesting electricity with microorganisms. Nat. Rev. Microbiol. 4, 497–508 (2006).
Lovley, D. et al. Humic substances as a mediator for microbially catalyzed metal reduction. Acta Hydrochim. Hydrobiol. 26, 152–157 (1998).
Scott, D. T., McKnight, D. M., Blunt-Harris, E. L., Kolesar, S. E. & Lovley, D. R. Quinone moieties act as electron acceptors in the reduction of humic substances by humics-reducing microorganisms. Environ. Sci. Technol. 32, 2984–2989 (1998).
Morita, M. et al. Potential for direct interspecies electron transfer in methanogenic wastewater digester aggregates. mBio 2, e00159–00111 (2011).
Yu, L., Tang, J., Zhang, R., Wu, Q. & Gong, M. Effects of biochar application on soil methane emission at different soil moisture levels. Biol. Fert. Soils 49, 119–128 (2013).
Inthapanya, S., Preston, T. & Leng, R. Biochar increases biogas production in a batch digester charged with cattle manure. Livest. Res. Rural Dev. 24, Article #212 (2012).
Das, K., Balagursamy, N., Chinnasamy, S., Martinez Castro, G. J. & Espino Lopez, C. in WO/2011/019871. (ed. WO Patent 2, 019,871) (WO Patent 2, 011,019,871, WO Patent 2,011,019,871; 2011).
Snook, G. A., Kao, P. & Best, A. S. Conducting-polymer-based supercapacitor devices and electrodes. J. Power Sources 196, 1–12 (2011).
van der Zee, F. P., Bisschops, I. A. E., Lettinga, G. & Field, J. A. Activated Carbon as an Electron Acceptor and Redox Mediator during the Anaerobic Biotransformation of Azo Dyes. Environ. Sci. Technol. 37, 402–408 (2002).
Cayuela, M. L. et al. Biochar and denitrification in soils: when, how much and why does biochar reduce N2O emissions? Sci. Rep. 3 (2013).
Joseph, S. D. et al. An investigation into the reactions of biochar in soil. Soil Res. 48, 501–515 (2010).
Heymann, K., Lehmann, J., Solomon, D., Schmidt, M. W. I. & Regier, T. C 1 s K-edge near edge X-ray absorption fine structure (NEXAFS) spectroscopy for characterizing functional group chemistry of black carbon. Org. Geochem. 42, 1055–1064 (2011).
Fan, W. et al. Hierarchical nanofabrication of microporous crystals with ordered mesoporosity. Nature Mater. 7, 984–991 (2008).
Du, K. et al. Self-Assembled Electrical Contact to Nanoparticles Using Metallic Droplets. Small 5, 1974–1977 (2009).
Araujo, J. C. et al. Comparison of hexamethyldisilazane and critical point drying treatments for SEM analysis of anaerobic biofilms and granular sludge. J. Electron. Microsc. 52, 429–433 (2003).
Smith, P. et al. Measurement of protein using bicinchoninic acid. Anal. Biochem. 150, 76–85 (1985).
We thank Trevor Woodard for facilitating HPLC and GC analysis; Louis Raboin for facilitating SEM analysis; Kenneth H. Williams and Baoshan Xing for providing biochar. The first author thanks the Oversea Study Program of Guangzhou Elite Project and the Innovative Dotorial Candidates Training Project of Sun Yat-sen University. This research was supported by the Office of Science (BER), U. S. Department of Energy, Award No. DESC0004485.
The authors declare no competing financial interests.
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Chen, S., Rotaru, AE., Shrestha, P. et al. Promoting Interspecies Electron Transfer with Biochar. Sci Rep 4, 5019 (2014). https://doi.org/10.1038/srep05019
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