The average contents of cellulose, hemicellulose, and lignin and total lignocellulose during the anaerobic co-digestion of corn stover and cow dung (55.0 ± 1.0°C) in the presence of different compound metals.
In the past decades, biotechnologies for reutilizing the biomass harvested from the metal-contaminated land draw attention to many scientists. Among those technologies, anaerobic fermentation is proven as an efficient conversion process for biowaste reduction with simultaneous recovery of biogas as an energy source. During the process of anaerobic fermentation, the release of metals from the biomass will impact the growth and performance of microorganisms in reactors, which then results the variation of substrate degradation. In this chapter, the impact of metals on the degradation of substrate at different stages of fermentation process, as indicated by variations of lignocelluloses, chemical oxygen demands (COD), volatile fatty acids (VFAs), etc., will be summarized. The objective is to rationalize the relationship between metal presence and substrate degradability and give suggestions for future research on metal-contaminated biomass reutilization.
- anaerobic fermentation
- heavy metal
- chemical oxygen demands
- volatile fatty acid
The rapid development of industries such as electronic, mining, agrochemical, tannery, and battery industries has led to an increase in the direct and indirect discharge of metals into the environment. Some metals are potentially toxic, and unlike some organic contaminants, they are not biodegradable; thus, they may accumulate in terrestrial and aquatic organisms . Hence, removal of potentially toxic metals (PTM) from contaminated environments has become an issue of urgent concern. In recent years, phytoremediation, which is defined as the use of plants to remove contaminants from contaminated environment, has drawn great attention probably because it is cost-effective and sustainable [2, 3]. However, disposing the biomass residues following phytoremediation is challenging [4, 5, 6]. Therefore, there has been a growing interest on the development of inexpensive disposal techniques and improvements in bio-resource utilization to foster sustainability in remediation systems .
Anaerobic fermentation is a relatively efficient conversion process for biomass waste reduction with simultaneous recovery of biogas as an energy source [8, 9, 10, 11]. In an anaerobic reactor, there are four processes that occur simultaneously, i.e., hydrolysis, acidogenesis, acetogenesis, and methanogenesis . Hydrolysis process involves the conversion of macromolecules such as proteins, polysaccharides, and fats that compose the cellular mass of the excess sludge into water-soluble molecules with a relatively small molecule (e.g., peptides, saccharides, and fatty acids) . Simple molecules with a low molecular weight such as volatile fatty acids (e.g., acetic, propionic, and butyric acid), alcohols, aldehydes, and gases like CO2, H2, and NH3 are produced via acidification of the hydrolyzed products (acidogenesis) . The acidification products are converted into acetic acids, H2 and CO2, by acetogenic bacteria in a process called acetogenesis. These first three steps of anaerobic digestion are often called acid fermentation, and they help transform the waste biomass into substrates for methanogenesis . In the methanogenesis process, the products of the acid fermentation (mainly acetic acid) are converted into CO2 and CH4.
Microorganisms responsible for anaerobic fermentation require a trace amount of metals (e.g., Ni, Co, Cu, Fe, Zn, etc.) for their optimum growth and performance . Various enzymes involved in anaerobic metabolism use trace metals as their cofactors. For example, methanogenic enzymes such as CO dehydrogenase (CODH) and methyl-H4MPT:HS-CoM methyltransferase use cobalt acts as their cofactor .
However, waste biomass often contains varying amounts of metals depending on the source of the biomass. During the process of anaerobic fermentation, the release of metals from the biomass will influence the efficiency of fermentation by affecting the enzyme activity, microorganism community, and even degradation and metabolic pathways . In this chapter, the impact of metals on the degradation of substrate, as indicated by variations of lignocelluloses, chemical oxygen demands, volatile fatty acids, etc., will be summarized. The objective is to rationalize the relationship between metal presence and substrate degradability during different fermentation stages and give suggestions for future research on metal-contaminated biomass reutilization.
2. Hydrolysis stage
Hydrolysis is oftentimes the rate-limiting step in the anaerobic digestion process probably because fermentative bacteria require an additional step of excreting extracellular enzymes, such as cellulases and lipases, to carry out the hydrolysis or solubilization process [16, 17]. It can be accelerated by enhancing the accessibility of anaerobic microorganisms to intracellular matter or cellulose using thermal, chemical, biological, and mechanical processes, as well as their combinations .
2.1 Lignocellulose degradation
Lignocelluloses are mainly composed of cellulose, hemicellulose, and lignin . The cellulose and hemicellulose themselves are relatively easy to be broken down by microorganisms; however, their biodegradability decreases when they occur in lignocellulose complexes . The impacts of metals on lignocellulose degradation vary with the metal species, concentrations, and fermentation conditions.
Previous studies showed that the presence of metals at certain concentrations may enhance the degradation of lignocelluloses [21, 22]. In one study, an average lignocellulose content of 87.49 ± 3.19%TS was obtained in a control group but decreased to 80.44 ± 3.41%TS, 77.94 ± 3.50%TS, and 79.45 ± 2.88%TS following the addition of 30, 100, and 500 mg/L Cu and 79.36 ± 3.72%TS, 79.10 ± 2.80%TS, and 76.60 ± 2.97%TS following the addition of 30, 100, and 500 mg/L Cr, respectively. Thus, Cu and Cr addition significantly enhanced the degradation of lignocellulose [21, 22].
Several studies on methanogenic bacteria found Cu, suggesting it could be a critical component for the enzymes super dismutase and hydrogenase . However, at relatively high concentrations, Cu can inhibit anaerobic fermentation, which results in reduction of degradation efficiency. Cu changes the physiological steady state of the fermentation process by inhibiting the degradation of the substrate and the growth of the microbes [8, 24]. In contrast, Cu has been shown to enhance the biogas production via fermentation [9, 25]. Despite the inhibitory effects of Cu, biogas production was probably enhanced by the addition of sulfide to the digester in stoichiometrically equivalent amounts . Our research suggested that the promoting effect of Cu addition on biogas yields was mainly attributable to better process stability, the enhanced degradation of lignin and hemicellulose, the transformation of intermediates into VFA, and the generation of CH4 from VFA .
Cr is one of the heavy metals that have often been blamed for unsatisfactory operation or failure of anaerobic digesters . Contradictory toxicity levels of Cr on anaerobic fermentation have been cited in literatures [28, 29]. This is probably because of differences in availability of Cr in fermenters (which is influenced by the precipitation and adsorption of soluble metals), differences in materials used in the studies , and dissimilar operational conditions (e.g., temperature, pH, hydraulic retention time, solid retention time, and mixed liquor volatile suspended solids) . Cr in certain concentrations was found to promote the efficient generation of CH4 by inducing better process stability, enhancing degradation of lignin and hemicellulose, transforming intermediates into VFA, and increasing coenzyme F420 activities .
According to our recent study, when compound metals were added into the fermentation reactors, the degradation of lignocelluloses performed differently (Table 1). It was found that the addition of Zn into the Cd- or Cu-containing reactors enhanced the degradation of lignin and cellulose significantly which resulted in a significant decrease in the total lignocellulose contents. The addition of Fe together with Cd reduced the cellulose contents and the total lignocellulose contents. In contrast, the addition of Ni into either Cd- or Cu-containing reactors did not improve the degradability of the feedstocks.
|Metals concentrations (mg/L)||Lignin
|Total lignocellulose (%TS)|
|Cd(1.0)||19.84 ± 0.94||13.14 ± 0.75||19.27 ± 1.38||52.25 ± 3.07|
|Cd(1.0) + Fe(10.0)||18.20 ± 0.63||11.96 ± 0.61||15.97 ± 0.90*||46.13 ± 2.14*|
|Cd(1.0) + Ni(2.0)||20.82 ± 1.10||15.02 ± 0.75||16.36 ± 0.60||52.20 ± 2.45|
|Cd(1.0) + Zn(2.0)||12.83 ± 1.07**||12.98 ± 0.64||13.55 ± 1.13**||39.36 ± 2.84**|
|Cu(1.0)||19.63 ± 0.85||13.23 ± 0.75||19.34 ± 1.46||52.21 ± 3.06|
|Cu(1.0) + Fe(10.0)||16.92 ± 0.90||11.44 ± 0.61||16.46 ± 0.83||44.83 ± 2.34**|
|Cu(1.0) + Ni(2.0)||19.95 ± 1.15||12.05 ± 0.69||20.21 ± 0.74||52.21 ± 2.58|
|Cu(1.0) + Zn(2.0)||14.56 ± 1.03**||12.34 ± 0.61||14.43 ± 1.18**||41.34 ± 2.82**|
Depending on the methanogenic pathway, the general trends of metal requirements are as follows: Fe is the most abundant metal, followed by Ni and Co and smaller amounts of Mo (and/or W) and Zn . Almost all metalloenzymes involved in the pathway of biogas production contain multiple Fe2S2, Fe3S4, or Fe4S4 clusters [17, 31, 32]. Fe is primarily present as Fe-S clusters used for electron transport and/or catalysis, as well as attenuating disturbances associated with the presence of sulfide which often results in a more stable process [31, 33, 34, 35]. Zn, like Cu, is present in relatively large concentrations in many methanogens. Zn is important in anaerobic fermentation because it is required by enzymes involved in methanogenesis such as coenzyme M methyltransferase . At certain concentrations, Zn can promote biogas production [37, 38]. For example, during the swine manure anaerobic digestion, Zn concentrations in the range of 125–1250 mg/L improved significantly microbial activity .
Ni is an important trace element for many prokaryotic microorganisms that are in the
2.2 Variation of chemical oxygen demands (COD)
The soluble organic components in the fermenter, shown as COD, originate from the hydrolysis process that liquefies large molecules; long-chain natural polymers of the substrate-like cellulose, hemicellulose, lignin, and polysaccharides; and proteins by extracellular enzymes [17, 44]. Previous studies on anaerobic fermentation of crops and manure showed that the COD in the reactor increased and then decreased because organic matter in the liquid was generated first and then consumed to produce the biogas. Therefore, greater COD did not cause greater biogas generation .
Previous studies demonstrated that COD initially increased and then decreased in the presence of Cu . During the initial stage of the fermentation, the substrate was rapidly hydrolyzed into small organic molecules, bringing about an increase of COD in the first 5 days. Later, the COD of the Cu-added groups decreased. The COD of the control group decreased more slowly than those of the Cu-added groups, and the discrepancy between them increased during the fermentation. Taking the whole fermentation process into account, the COD in the Cu addition groups were relatively lower than the control group. It was suggested that Cu addition enhanced the utilization of organic molecules in the fermentation (as indicated by the decrease of COD) and the biogas production . A similar promoting effect was found in the Cr-stressed anaerobic fermentation process . However, Cr addition did not yield lower COD than the control group.
The COD were generally lower in Fe-added groups than in the control group . Fe addition induced a stable and excellent COD conversion rate suggesting a more efficient utilization of soluble organic components in the fermenter that consequently improves biogas yields . Likewise, Ni addition influenced the biogas production, and this can also be partly explained by the Ni effect on COD . Lower COD concentrations and higher biogas yields were obtained using higher Ni concentrations. The results demonstrated the balance of different fermentation steps (from hydrolysis to methanogenic phase). Moreover, as the substrates in the Ni-added groups were better degraded in the former three stages (from 4th to 13th day), the left substrates were few, and hence the COD concentrations of Ni-added groups were not increased at the end of the experiments.
The variation of COD in the presence of metals should also be considered under different fermentation temperatures. The required amounts for Ni, Co, Zn, and Fe and in thermophilic glucose fermentation were 10 times more than those required for mesophilic acetate fermentation [49, 50]. In our anaerobic fermentation experiment with acid-pretreated corn stover mixed with fresh cow dung as feedstocks, the COD at 55, 45, 35, and 25 ± 1.0°C were analyzed with and without Cd (1.0 mg/L) addition. The cumulative biogas yields and average COD during the entire fermentation process in Cd-added and no Cd-added group are shown in Table 2. It was found that Cd addition resulted in higher biogas yields with the increase of temperature together with the lower COD. Overall, the biogas production should be explained by the variation and/or consumption of the COD concentrations along with VFAs during the fermentation process, rather than the values of COD concentrations.
|Treatments||Parameters||55.0 ± 1.0°C||45.0 ± 1.0°C||35.0 ± 1.0°C||25.0 ± 1.0°C|
|No Cd added||COD (mg/L)||10172.01 ± 1246.81||11219.30 ± 1596.13||12116.95 ± 2317.61||9517.14 ± 1199.70|
|Biogas yield (mL/g TS)||67.65 ± 1.16||58.45 ± 1.01||19.42 ± 0.32||15.96 ± 0.27|
|Cd added||COD(mg/L)||9651.83 ± 1505.46||11052.13 ± 1612.40||13192.66 ± 2518.87||9829.71 ± 398.46|
|Biogas yield (mL/g TS)||341.62 ± 5.88||68.35 ± 1.18||20.51 ± 0.34||15.84 ± 0.27|
3. Acidogenesis stage
Acidification is affected by a very diverse group of bacteria, the majority of which are strictly anaerobic. As the acidogenesis stage progresses, the acidic components, including long-chain fatty acids (LCFAs), volatile fatty acids (VFAs), etc., are generated, and they cause a change in the pH. Furthermore, during acidogenesis, organic nitrogen is converted into ammonia .
3.1 Variation of pH values
The optimal pH range for efficient methanogenesis ranges from 6.7 to 7.4 . However, the acidogenic bacteria can metabolize organic material down to a pH of around 4. At the beginning of anaerobic fermentation, the pH values are likely to decrease due to the generation of acid components. Thus, buffer solution is suggested for preventing the dramatic pH reduction.
On the one hand, the effect of metal toxicity depends on pH . In general, at high pHs metals have a tendency to form insoluble metal phosphates and carbonates , whereas at low pHs the initial leaching of metals from the sludge occurs and hence their solubility increases [55, 56]. Soluble levels of Ni ion were found the highest, while those of Pb ions were found the least as compared to other four heavy metals from pH 4 to 12. At extreme pH of 1, Zn, Pb, and Cd ions showed higher levels than those of Ni, Cu, and Cr. However, Cu, Ni, and Zn ion levels were found higher than those of Pb, Cd, and Cr at an extreme pH of 13. Metal ion levels showed the order of Ni > Cu > Cr > Zn > Cd > Pb between pH 8 and 12. In other pH ranges, metal ions varied with pH .
On the other hand, the presence of metals in the reactor during the fermentation process can modify pH values. Previous studies found that adding Cu and Cr resulted in a decrease in pH at the beginning of the experiment, but the pH later recovered [21, 22]. The average pH following addition of Cu have been shown to be generally higher than control groups as well as groups in which Cr is added. An investigation on anaerobic digestion of sewage sludge found that pH negatively related with the exchangeable (−0.838, p < 0.01) and residual fractions (−0.753, p < 0.01) of Cu while positively related to Fe-Mn oxide-bound (0.895, p < 0.01) and organic-bound (0.698, p < 0.05) fractions of Cu . In contrast, pH positively related to carbonate-bound Cr (0.768, p < 0.01) and organic-bound Cr (0.908, p < 0.01) while negatively related to Fe-Mn oxide-bound Cr (−0.899, p < 0.01) . The results suggest the decrease of pH at the beginning of fermentation was probably beneficial for generating both the exchangeable and residual fractions of Cu. The increase of pH after the start-up of the fermentation is probably helpful for partitioning Cr to yield carbonate-bound and organic-bound fractions, thus reducing the bioavailability and toxicity of Cr .
Addition of Fe and Ni has been shown promote an alkalescent environment for anaerobic fermentation. Previous studies found that adding 10.0 mg/L Fe into the fermenter resulted in lower pH values (p < 0.05) when fermentation is around its peak stage . However, following fermentation peak stage, no significant change in pH has been reported even after increasing the Fe concentration from 0.5 to 5.0 mg/L or Ni concentrations from 0.2 to 2.0 mg/L [46, 48].
3.2 Variation of NH4+-N concentrations
Total ammonia (TAN), consisting of ammonium ions (NH4+) and free ammonia (FAN, NH3), is produced during anaerobic degradation of proteins, urea, and nucleic acids . At NH4+-N concentrations below 200 mg/L, TAN is an important nutrient for microorganism growth . However, it was reported by Math-Alvarez et al.  and confirmed in a critical review by Chen et al.  that NH4+-N concentrations ranging from 0.6 to 14 g/L inhibited the methanogenic activity depending on different experimental conditions .
Previous studies showed that Cu or Cr addition induced remarkable differences in NH4+-N concentrations compared to a control group [21, 22]. The NH4+-N values in the control group fluctuated in the range 9.70–157.34 mg/L before the 21st day of fermentation; yet in Cu- and Cr-added groups, the NH4+-N values were relatively stable with concentrations ranging from 55.98 to 113.82 mg/L  and 39.85 to 105.87 mg/L , respectively. Thus, Cu and Cr addition contributed to the stability of the fermentation system.
Table 3 shows that further addition of other metals may increase the NH4+-N concentrations in the metal-stressed fermenters. According to our research, Zn addition significantly enhanced the generation of NH4+-N in both Cd and Cu contained fermenters. Addition of Ni induced higher NH4+-N concentrations in Cd-stressed anaerobic fermentation process, while Fe had a similar response in Cu-stressed fermentation processes. The results suggest that metal mixtures benefited from the degradation of substrate containing nitrogen, such as proteins (Table 3) together with the degradation of lignocelluloses (Table 1).
|Metals concentrations (mg/L)||NH4+-N||Total VFAs|
|Cd(1.0)||558.39 ± 39.25||910.57 ± 273.75|
|Cd(1.0) + Fe(10.0)||604.50 ± 37.34||1865.18 ± 684.94|
|Cd(1.0) + Ni(2.0)||747.13 ± 38.21**||1003.57 ± 219.79|
|Cd(1.0) + Zn(2.0)||675.34 ± 36.22*||513.86 ± 195.52|
|Cu(1.0)||476.63 ± 37.36||369.77 ± 73.28|
|Cu(1.0) + Fe(10.0)||652.83 ± 61.88*||1562.24 ± 577.63*|
|Cu(1.0) + Ni(2.0)||569.31 ± 23.62||1029.20 ± 298.17|
|Cu(1.0) + Zn(2.0)||671.82 ± 43.40**||804.66 ± 286.14|
3.3 Variation of long-chain fatty acids (LCFAs)
Long-chain fatty acids (LCFAs) are the intermediate products of lipids’ hydrolysis and thus are abundant in lipid-rich substrates such as slaughterhouse wastewater and dairy industrial sludge [63, 64]. LCFAs (e.g., oleic acid) are often degraded through β-oxidation  to form acetate, hydrogen, and short-chain fatty acids (SCFAs). Short-chain fatty acids are further catabolized to acetate and hydrogen following cycles of β-oxidation . LCFAs can inhibit the activities of the microorganisms involved in all the AD steps  by attaching to bacterial cell membrane, thus limiting mass transfer . It was reported that LCFAs concentration of 0.2 g/L oleate had a profound inhibitory effect, while biogas production ceased when the concentration was increased to 0.5 g/ L . Hwu et al.  reported 50% inhibition of methanogenesis in batch reactors at 0.1–0.9 g L−1 oleate, depending on the origin of the bacterial inoculum. It has been previously documented that LCFAs could inhibit the activity of hydrolytic, acidogenic, and acetogenic bacteria and methanogenic archaea [68, 69, 71]. However, many studies have reported an adaptation of the microbial communities during the degradation of LCFAs [70, 72]. Moreover, the archaeal community was found to be more tolerant to increased LCFA concentration levels compared to the bacterial community .
Metals play a major role in several metabolic pathways and thus will impact of transformation of LCFAs during fermentation process. In general, adding adequate concentrations of microelements may accelerate the degradation of short-chain fatty acids (SCFAs) and LCFAs and would be beneficial for the anaerobic mono-digestion of food waste . However, there is lack of studies on the responses of LCFAs to metal stress. Further studies are necessary for revealing the underlying mechanisms.
3.4 Variation of total volatile fatty acids
VFAs are the intermediary products of the anaerobic fermentation and a precursor for methanogenesis. The concentration of VFA is an important index to evaluate the efficiency of hydrolysis, acidification, and methanogenesis . Trace metal supplementation is one method to increase VFA utilization .
Many studies worked on the impacts of heavy metals on the degradation of VFAs [77, 78, 79]. At the beginning of the fermentation, the total VFAs often increase due to hydrolysis of substrate and the accumulation of acidic hydrolytic products [21, 22], together with the decrease of pH values. It was reported that a pH range of 5.7–6.0 was recommended as optimal to produce VFAs . During this period, high concentration of Cu was found to inhibit the acidification process , while high concentration of Cr inhibited the methanogenesis , resulting in low biogas yields. Later on, the VFAs were shown to be consumed during the biogas production, and supplementing metals greatly benefited the process [21, 22].
Supplementing metals may promote the degradation of VFAs, while a metal deficiency may result in the accumulation of VFAs, which often inhibits the anaerobic processes. For example, a previous study found Fe and Ni deficiency during anaerobic digestion of wheat stillage resulted in a rapid accumulation of VFAs . In another study, excluding Co, Zn, and Ni from the methanol-based feed of an UASB reactor induced lower specific methanogenic activity (SMA) and the accumulation of VFAs [82, 83, 84].
A strong relationship has been previously reported between VFAs and different forms of metals . For example, there was a strong correlation between the organic-bound Cr and VFAs (
4. Acetogenesis stage
Many factors, including substrate concentration, hydraulic retention time, temperature, pH, and process configuration, affect the performance of the acidogenesis phase [31, 85]. However, these factors are particularly susceptible to the presence and subsequent interactions with heavy metal ions .
The C2-C7 organic acids are predominant intermediates in the anaerobic digestion of organic matter. The anaerobic oxidation of the C3-C7 substrates is coupled to a reduction of protons (H2 formation), and the oxidation of C3 and C4 organic acids is thermodynamically unfavorable (endergonic process) under standard conditions .
Lin studied the effects of Cr, Cd, Pb, Cu, Zn, and Ni on VFA degradation in anaerobic digestion by using serum bottle assays with acetic acid acclimated seed sludge (AASS) and mixed acid acclimated seed sludge (MASS) . The relative toxicity of heavy metals to degradation of acetic acid (HAc), propionic acid (HPr), and n-butyric acid (n-HBu) was Cd > Cu > Cr > Zn > Pb > Ni, Cd > Cu > ≒ Zn ≒ Cr > Pb > Ni, and Cd > Cu > Cr > Zn > Pb > Ni, respectively . Cd and Cu were the most, and Pb and Ni were the least toxic heavy metals to VFA-degrading organisms. To some heavy metals, VFA-degrading acetogens were more sensitive than HAc-utilizing methanogens. The order of sensitivity of the VFA degradation to the metallic inhibition was HPr > HAc ≒ HBu for Cr, HAc > HPr ≒ HBu for Cd and Pb, HPr > HAc > HBu for Zn, HAc ≒ HPc ≒ HBu for Cu, and HAc > HPR > HBu for Ni. Mixtures of the heavy metals caused synergistic inhibition on HAc degradation .
Lin et al. carried out a systematic study on the effect of trace metal supplementation on anaerobic degradation of butyric acid . The results showed that the stimulatory effects were in the following order: Cu2+ < Fe3+ < Zn2+ < Ni 2+ < Mn2+ and the normal and isoHBu degradation activities of the methanogens increased by 14–25% and 17–43%, respectively . Kim et al. reported that the supplementation of Ca, Fe, Co, and Ni to a thermophilic non-mixed reactor was required in order to achieve a high conversion of propionate at high concentrations of VFAs .
About 70% of CH4 is generated from acetic acid . The acetate utilization rates required per gram of VSS are used to estimate the nutrient supplementation required to prevent limitations in methanogenic activity . Addition of Fe was found to have a stimulatory effect on acetate utilization by methanogens . Bhattacharya et al.  found adding 20 mg/L Zn2+ resulted in a complete inhibition of acetate degradation due to Zn toxicity to methanogenesis. Ni sites in the acetyl-CoA decarboxylase/synthase enzyme complex have been identified. This enzyme seemed to have an important role in the conversion of acetate to CH4 .
5. Methanogenesis stage
Methanogenesis is the microbial process, whereby CO2, acetate, or methyl compounds are converted to CH4 in order to generate ATP through the buildup of a sodium ion or proton gradient . Methanogenesis is one of the most metal-rich enzymatic pathways in biology . The contents of Cu, Fe, Ni, and Zn in methanogens (including 10 species of
5.1 Biogas yields
The stimulatory effect of trace metal supplementation in certain ranges on anaerobic digestion has been widely reported [10, 21, 46]. Depending on the methanogenic pathway, the general trends of metal requirements are as follows: Fe is the most abundant metal, followed by Ni and Co and smaller amounts of Mo (and/orW) and Zn .
Low concentrations of Fe have been shown to markedly increase the conversion of acetic acid to CH4 . Fe2+ in concentrations of up to 20 mM has been shown to increase the conversion of acetate to CH4 . It was found that Fe2+ marginally stimulated biogas yield and CH4 content at 37°C and the addition of Fe2+ increased VFA utilization but enhanced H2 utilization considerably . The addition of Fe resulted in a stable process, and its combination with Co contributed to higher biogas production (+9%), biogas production rates (+35%), and reduced VFA concentration while simultaneously degrading the organic fraction of municipal solid waste and slaughterhouse waste . The promoting effect of Fe2+ addition on biogas yields of mixed
The optimum or stimulatory concentrations of Ni for batch cultures of methanogens were reported to range between 12 mg/m3 and 5 g/m3 . Pobeheim et al. observed an increase in CH4 production of 25% at day 25 of operation following addition of 10.6 μM Ni . Ni addition of 1–200 μM enhanced the methane production from anaerobic conversion of acetate by 6.30–44.6% compared with the control, respectively . Furthermore, the limitation of Ni in the fermenters led to process instability and was proven to reduce biogas generation . On the other hand, the addition of Ni was found to be beneficial to the methanation process. Ni had increased the ratio of CH4:CO2 .
Besides Fe, Ni, and Co, other trace metals like Cu, Cr, and Cd were shown to promote biogas production. Lower concentrations of Cu (1.82 ± 0.01 μg/g dry wt.) and Cr (0.89 ± 0.04 μg/g dry wt.) better served as micronutrients for methanogenic bacteria and might have enhanced the process of methanogenesis and thus CH4 content in the product biogas . Cao et al. harvested five types of plant from Cu-contaminated land, including
5.2 Biogas compositions
Biogas is composed of CH4, CO2, and other trace compositions like H2. Methanogens using H2/CO2 as the matrix usually contain two hydrogenases: one is a hydrogenase that uses coenzyme F420 as the electron acceptor called coenzyme F420-reducing hydrogenase, and the other is coenzyme F420-nonreducing hydrogenase . Hence, the presence of metals in the fermenters influences the biogas composition by impacting the pathways. For example, Cu2+ and Cr6+ addition stimulated biogas production and the generation of CH4 by enhancing the activities of coenzyme F420 and methanogenesis [21, 22].
Previously, Fe was found in acetyl-CoA synthase, CH4 monooxygenase, NO-reductase, and nitrite reductase . Fe, together with Ni, was found in hydrogenases of
As we studied, the compositions of biogas varied with temperatures in the presence of heavy metals. The impacts of Cd addition on biogas compositions of anaerobic co-digestion of acid-pretreated corn and fresh cow dung under different fermentation temperatures are shown in Figure 1. When temperature increased, the CH4, CO2, and H2 contents also increased, but N2 contents decreased in both Cd-added and control groups. The CH4 contents reached plateau after the fourth day in 55°C group and seventh day in 45°C group (Figure 1A). The increase of CO2 contents slowed down after the fourth day in both 55 and 45°C groups (Figure 1B). The tendency of CH4 and CO2 contents in 35 and 25°C groups was not detected fully as the biogas yields were too low to be collected by gas bag. Similar contents of H2 were observed in 45, 35, and 25°C groups while lower in 55°C group (Figure 1C). The N2 contents decreased more rapidly when fermentation temperature was increased (Figure 1D). The results indicated that elevated temperatures accelerated the start-up of fermentation.
Cd addition improved the CH4 contents by approximately 6% after the fourth day in 55°C group. Taking the other biogas compositions into account, it was found that Cd addition decreased the CO2 contents in the biogas while having little influences on H2 and N2 contents. However, the impact of Cd on biogas compositions in other three temperature groups was not significant. Therefore, thermophilic fermentation (55°C) promoted the CH4 generation in the presence of Cd in the present study. Low temperature hindered the production of CH4 which agreed with a previous study that used swine manure as substrate .
This book chapter reviewed the past findings in the impacts of metals on different stages of the anaerobic degradation process. The requirements of metals by the enzymes involved in the anaerobic process resulted in the different performances with varied metal species and bioavailability. In general, metals in certain concentrations were able to promote the lignocellulose degradation, the generation and consumption of organic components in the fermenters like LCFAs and VFAs, the biogas production, as well as the CH4 contents. The mechanisms of metals were studied by many scientists, focusing on the enzyme activities, microbial communities, etc.
Although a large amount of research has been carried out on individual stages or the entire anaerobic fermentation process, there are still challenges on controlling metal-stressed anaerobic degradation process for optimal utilization of metal-contaminated biowastes. Further work on bioavailability of metals during anaerobic fermentation process and detailed compositions of intermediary products, the relationships between microbial functions and metal species, etc. are recommended for better understanding of the metal-stressed anaerobic degradation process.
This work was funded by the Major Science and Technology Program for Water Pollution Control and Treatment (No. 2017ZX07101-003, 2015ZX07204-007, 2015ZX07203-011), the Fundamental Research Funds for the Central Universities (2018MS051).
Conflict of interest
No conflict of interest.
Fu FL, Wang Q. Removal of heavy metal ions from wastewaters: A review. Journal of Environmental Management. 2011; 92:407-418. DOI: 10.1016/j. jenvman.2010.11.011
Bauddh K, Singh RP. Cadmium tolerance and its phytoremediation by two oil yielding plants Ricinus communis(L.) and Brassica juncea(L.) from the contaminated soil. International Journal of Phytoremediation. 2012; 14:772-785. DOI: 10.1080/15226514.2011.619238
Lakshmi PM, Jaison S, Muthukumar T, Muthukumar M. Assessment of metal accumulation capacity of Brachiaria ramosacollected from cement waste dumping area for the remediation of metal contaminated soil. Ecological Engineering. 2013; 60:96-98. DOI: 10.1016/j.ecoleng.2013.07.043
Sas-Nowosielska A, Kucharski R, Małkowski E, Pogrzeba M, Kuperberg JM, Kryński K. Phytoextraction crop disposal-an unsolved problem. Environmental Pollution. 2004; 128:373-379. DOI: 10.1016/j.envpol.2003.09.012
Ghosh M, Singh SP. A review on phytoremediation of heavy metals and utilization of it’s by products. Applied Ecology and Environmental Research. 2005; 6:214-231. DOI: 10.15666/aeer/0301_001018
Carrier M, Loppinet-Serani A, Absalon C, Marias F, Aymonier C, Mench M. Conversion of fern ( Pteris vittataL.) biomass from a phytoremediation trial in sub-and supercritical water conditions. Biomass and Bioenergy. 2011; 35:872-883. DOI: 10.1016/j.biombioe.2010.11.007
Kobayashi T, Wu YP, Lu ZJ, Xu KQ. Characterization of anaerobic degradability and kinetics of harvested submerged aquatic weeds used for nutrient phytoremediation. Energies. 2015; 8:304-318. DOI: 10.3390/en8010304
Yue Z-B, Yu H-Q , Wang Z-L. Anaerobic digestion of cattail with rumen culture in the presence of heavy metals. Bioresource Technology. 2007; 98:781-786. DOI: 10.1016/j.biortech.2006.03.017
Verma VK, Singh YP, Rai JPN. Biogas production from plant biomass used for phytoremediation of industrial wastes. Bioresource Technology. 2007; 98:1664-1669. DOI: 10.1016/j.biortech.2006.05.038
Zhang HY, Tian YL, Wang LJ, Zhang LY, Dai LM. Ecophysiological characteristics and biogas production of cadmium-contaminated crops. Bioresource Technology. 2013; 146:628-636. DOI: 10.1016/j.biortech.2013.07.148
Tian YL, Zhang HY. Producing biogas from agricultural residues generated during phytoremediation process: Possibility, threshold, and challenges. International Journal of Green Energy. 2016; 13:1556-1563. DOI: 10.1080/15435075.2016.1206017
van Haandel AC, der Lubbe JGM, editors. Handbook Biological Wastewater Treatment-Design and Optimization of Activated Sludge Systems. London: IWA Publishing; 2007. pp. 377-380. DOI: 10.2166/9781780400808
Manyiloh CE, Mamphweli SN, Meyer EL, Okoh AI, Makaka G, Simon M. Microbial anaerobic digestion (bio-digesters) as an approach to the decontamination of animal wastes in pollution control and the generation of renewable energy. International Journal of Environmental Research and Public Health. 2013; 10:4390-4417. DOI: 10.3390/ijerph10094390
Wyman V, Serrano A, Fermoso FG, Villa Gomez DK. Trace elements effect on hydrolytic stage towards biogas production of model lignocellulosic substrates. Journal of Environmental Management. 2019; 234:320-325. DOI: 10.1016/j.jenvman.2019.01.015
Zandvoort BMH, Van HED, Fermoso FG, Lens PNL. Trace metals in anaerobic granular sludge reactors: Bioavailability and dosing strategies. Engineering in Life Sciences. 2006; 6:293-301. DOI: 10.1002/elsc.200620129
Bayer EA, Lamed R, Himmel ME. The potential of cellulases and cellulosomes for cellulosic waste management. Current Opinion in Biotechnology. 2007; 18:237-245. DOI: 10.1016/j.copbio.2007.04.004
Mudhoo A, Kumar S. Effects of heavy metals as stress factors on anaerobic digestion processes and biogas production from biomass. International Journal of Environmental Science and Technology. 2013; 10:1383-1398. DOI: 10.1007/ s13762-012-0167-y
Barua VB, Goud VV, Kalamdhad AS. Microbial pretreatment of water hyacinth for enhanced hydrolysis followed by biogas production. Renewable Energy. 2018; 126:21-29. DOI: 10.1016/j.renene.2018.03.028
Taherzadeh MJ, Karimi K. Pretreatment of lignocellulosic wastes to improve ethanol and biogas production: A review. International Journal of Molecular Sciences. 2008; 9:1621-1651. DOI: 10.3390/ijms9091621
Pokój T, Bułkowska K, Gusiatin ZM, Klimiuk E, Jankowski KJ. Semi-continuous anaerobic digestion of different silage crops: VFAs formation, methane yield from fiber and non-fiber components and digestate composition. Bioresource Technology. 2015; 190:201-210. DOI: 10.1016/j.biortech.2015.04.060
Zhang HY, Han XX, Tian YL, Li Y, Yang K, Hao H, et al. Process analysis of anaerobic fermentation of Phragmites australisstraw and cow dung exposing to elevated chromium (VI) concentrations. Journal of Environmental Management. 2018; 224:414-424. DOI: 10.1016/j.jenvman.2018.07.058
Hao H, Tian YL, Zhang HY, Chai Y. Copper stressed anaerobic fermentation: Biogas properties, process stability, biodegradation and enzyme responses. Biodegradation. 2017; 28:369-381. DOI: 10.1007/s10532-017-9802-0
Kayhanian M, Rich D. Pilot-scale high solids thermophilic anaerobic digestion of municipal solid waste with an emphasis on nutrient requirements. Biomass and Bioenergy. 1995; 8:433-444. DOI: 10.1016/0961-9534(95)00043-7
Lenártová V, Holovská K, Javorský P. The influence of mercury on the antioxidant enzyme activity of rumen bacteria Streptococcus bovisand Selenomonas ruminantium. FEMS Microbiology Ecology. 1998; 27:319-325. DOI: 10.1016/S0168-6496(98)00077-4
Cao Z, Wang S, Wang T, Chang Z, Shen Z, Chen Y. Using contaminated plants involved in phytoremediation for anaerobic digestion. International Journal of Phytoremediation. 2015; 17:201-207. DOI: 10.1080/15226514.2013.876967
Lawrence AW, McCarty PL. The role of sulfide in preventing heavy metal toxicity in anaerobic treatment. Water Pollution Control Federation. 1965; 37:392-406. DOI: 10.2307/25035257
Alkan U, Anderson GK, Ince O. Toxicity of trivalent chromium in the anaerobic digestion process. Water Research. 1996; 30:731-741. DOI: 10.1016/ 0043-1354(95)00181-6
Kouzeli-Katsiri A, Kartsonas N, Priftis A. Assessment of the toxicity of heavy metals to the anaerobic digestion of sewage sludge. Environmental Technology Letters. 1988; 9:261-270. DOI: 10.1080/09593338809384566
Hayes TD, Theis TL. The distribution of heavy metals in anaerobic digestion. Water Pollution Control Federation. 1978; 50:61-72. DOI: 10.2307/25039507
Karri S, Sierra-alvarez R, Field JA. Toxicity of copper to acetoclastic and hydrogenotrophic activities of methanogens and sulfate reducers in anaerobic sludge. Chemosphere. 2006; 62:121-127. DOI: 10.1016/j.chemosphere.2005.04. 016
Glass JB, Orphan VJ. Trace metal requirements for microbial enzymes involved in the production and consumption of methane and nitrous oxide. Frontiers in Microbiology. 2012; 3:1-20. DOI: 10.3389/fmicb.2012.00061
Jackson-Moss CA, Duncan JR. The effect of iron on anaerobic digestion. Biotechnology Letters. 1990; 12:149-154. DOI: 10.1007/bf01022433
Bayr S, Pakarinen O, Korppoo A, Liuksia S, Väisänen A, Kaparaju P, et al. Effect of additives on process stability of mesophilic anaerobic monodigestion of pig slaughterhouse waste. Bioresource Technology. 2012; 120:106-113. DOI: 10.1016/j.biortech.2012.06.009
Moestedt J, Nordell E, Shakeri Yekta S, Lundgren J, Martí M, Sundberg C, et al. Effects of trace element addition on process stability during anaerobic co-digestion of OFMSW and slaughterhouse waste. Waste Management. 2016; 47:11-20. DOI: 10.1016/j.wasman.2015.03.007
Nordell E, Nilsson B, Påledal SN, Karisalmi K, Moestedt J. Co-digestion of manure and industrial waste-the effects of trace element addition. Waste Management. 2016; 47:21-27. DOI: 10.1016/j.wasman.2015.02.032
Scherer P, Lippert H, Wolff G. Composition of the major elements and trace elements of 10 methanogenic bacteria determined by inductively coupled plasma emission spectrometry. Biological Trace Element Research. 1983; 5:149-163. DOI: 10.1007/BF02916619
Anuj K, Miglani P, Gupta RK, Bhattacharya TK. Impact of Ni(II), Zn(II) and Cd(II) on biogassification of potato waste. Journal of Environmental Biology. 2006; 27:61-66. DOI: 10.2112/05A-0018.1
Patel VB, Patel AR, Patel MC, Madamwar DB. Effect of metals on anaerobic digestion of water hyacinth-cattle dung. Applied Biochemistry and Biotechnology. 1993; 43:45-50. DOI: 10.1007/bf02916429
Zhang R, Wang X, Gu J, Zhang Y. Influence of zinc on biogas production and antibiotic resistance gene profiles during anaerobic digestion of swine manure. Bioresource Technology. 2017; 244:63-70. DOI: 10.1016/j.biortech.2017.07.032
Sawers RG. Nickel in bacteria and archaea. In: Kretsinger RH, Uversky VN, Permyakov EA, editors. Encyclopedia of Metalloproteins. New York: Springer-Verlag; 2013. pp. 1490-1496. DOI: 10.1007/978-1-4614-1533-6_86
Ragsdale SW. Nickel-based enzyme systems. The Journal of Biological Chemistry. 2009; 284:18571-18575. DOI: 10.1074/jbc.R900020200
Chen Y, Cheng JJ, Creamer KS. Inhibition of anaerobic digestion process: A review. Bioresource Technology. 2008; 99:4044-4064. DOI: 10.1016/j.biortech. 2007.01.057
Ahring BK, Westermann P. Sensitivity of thermophilic methanogenic bacteria to heavy metals. Current Microbiology. 1985; 12:273-276. DOI: 10.1007/ bf01567977
Tabatabaei M, Sulaiman A, Nikbakht AM, Yusof N, Najafpour G. Influential parameters on biomethane generation in anaerobic wastewater treatment plants. In: Manzanera M, editor. Alternative Fuel. London: IntechOpen; 2011. pp. 227-262. DOI: 10.5772/24681
Chakraborty N, Chatterjee M, Sarkar GM, Lahiri SC. Inhibitory effects of the divalent metal ions on biomethanation by isolated mesophilic methanogen in AC21 medium in presence or absence of juices from water hyacinth. Bioenergy Research. 2010; 3:314-320. DOI: 10.1007/s12155-010-9083-5
Zhang HY, Tian YL, Wang LJ, Mi XY, Chai Y. Effect of ferrous chloride on biogas production and enzymatic activities during anaerobic fermentation of cow dung and Phragmitesstraw. Biodegradation. 2016; 27:69-82. DOI: 10.1007/ s10532-016-9756-7
Vlyssides A, Barampouti EM, Mai S. Influence of ferrous iron on the granularity of a UASB reactor. Chemical Engineering Journal. 2009; 146:49-56. DOI: 10.1016/j.cej.2008.05.011
Tian YL, Zhang HY, Chai Y, Wang LJ, Mi XY, Zhang LY, et al. Biogas properties and enzymatic analysis during anaerobic fermentation of P hragmites australisstraw and cow dung: Influence of nickel chloride supplement. Biodegradation. 2017; 28:15-25. DOI: 10.1007/s10532-016-9774-5
Takashima M, Speece RE. Mineral nutrient requirements for high-rate methane fermentation of acetate at low SRT. Research Journal of the Water Pollution Control Federation. 1989; 61:1645-1650. DOI: 10.1016/0034-4257(89)90059-X
Takashima M, Shimada K, Speece RE. Minimum requirements for trace metals (iron, nickel, cobalt, and zinc) in thermophilic and mesophilic methane fermentation from glucose. Water Environment Research. 2011; 83:339-346. DOI: 10.2175/106143010x12780288628895
Kayhanian M. Ammonia inhibition in high-solids biogasification: An overview and practical solutions. Environmental Technology. 1999; 20:355-365. DOI: 10.1080/09593332008616828
Bitton G, editor. Wastewater Microbiology. 3rd ed. Chichester: Wiley; 2005. 1132 p. DOI: 10.1146/annurev.mi.30.100176.001403
Lin CY, Chen CC. Effect of heavy metals on the methanogenic UASB granule. Water Research. 1999; 33:409-416. DOI: 10.1016/s0043-1354(98)00211-5
Rensing C, Maier RM. Issues underlying use of biosensors to measure metal bioavailability. Ecotoxicology and Environmental Safety. 2003; 56:140-147. DOI: 10.1016/s0147-6513(03)00057-5
Gonzalez-Gil G, Lopes SI, Saikaly PE, Lens PN. Leaching and accumulation of trace elements in sulfate reducing granular sludge under concomitant thermophilic and low pH conditions. Bioresource Technology. 2012; 126:238-246. DOI: 10.1016/j.biortech.2012.09.044
Zandvoort MH, Van Hullebusch ED, Peerbolte A, Golubnic S, Lettinga G, Lens PNL. Influence of pH shocks on trace metal dynamics and performance of methanol fed granular sludge bioreactors. Biodegradation. 2005; 16:549-567. DOI: 10.1007/s10532-004-7789-9
Lo HM, Lin KC, Liu MH, Pai TZ, Lin CY, Liu WF, et al. Solubility of heavy metals added to MSW. Journal of Hazardous Materials. 2009; 161:294-299. DOI: 10.1016/j.jhazmat.2008.03.119
Zhang M, Yang C, Jing Y, Li J. Effect of energy grass on methane production and heavy metal fractionation during anaerobic digestion of sewage sludge. Waste Management. 2016; 58:316-323. DOI: 10.1016/j.wasman.2016.09.040
Rajagopal R, Massé DI, Singh G. A critical review on inhibition of anaerobic digestion process by excess ammonia. Bioresource Technology. 2013; 143:632-641. DOI: 10.1016/j.biortech.2013.06.030
Liu T, Sung S. Ammonia inhibition on thermophilic aceticlastic methanogens. Water Science and Technology. 2002; 45:113-120. DOI: 10.2166/wst.2002.0304
Math-Alvarez J, Mtz.-Viturtia A, Llabrés-Luengo P, Cecchi F. Kinetic and performance study of a batch two-phase anaerobic digestion of fruit and vegetable wastes. Biomass and Bioenergy. 1993; 5:481-488. DOI: 10.1016/0961-9534(93) 90043-4
Tian H, Karachalios P, Angelidaki I, Fotidis IA. A proposed mechanism for the ammonia-LCFA synergetic co-inhibition effect on anaerobic digestion process. Chemical Engineering Journal. 2018; 349:574-580. DOI: 10.1016/j.cej.2018. 05.083
Wu LJ, Kobayashi T, Kuramochi H, Li YY, Xu KQ , Lv Y. High loading anaerobic co-digestion of food waste and grease trap waste: Determination of the limit and lipid/long chain fatty acid conversion. Chemical Engineering Journal. 2018; 338:422-431. DOI: 10.1016/j.cej.2018.01.041
Stoll U, Gupta H. Management strategies for oil and grease residues. Waste Management and Research. 1997; 15:23-32. DOI: 10.1177/0734242X9701500103
Jezzard P, LeBihan D, Cuenod C, Pannier L, Prinster A, Turner R. An investigation of the contributions of physiological noise in human functional MRI studies at 1.5 Tesla and 4 Tesla. In: Proceedings of Society of Magnetic Resonance in Medicine (SMRM), 12th Annual Meeting; 14-20 August 1993; New York. Berlin: Springer; 1993. p. 1392
Lalman JA, Bagley DM. Anaerobic degradation and inhibitory effects of linoleic acid. Water Research. 2000; 34:4220-4228. DOI: 10.1016/s0043-1354(00)00180-9
Cirne DG, Paloumet X, Björnsson L, Alves MM, Mattiasson B. Anaerobic digestion of lipid-rich waste-effects of lipid concentration. Renewable Energy. 2007; 32:965-975. DOI: 10.1016/j.renene.2006.04.003
Pereira MA, Pires OC, Mota M, Alves MM. Anaerobic biodegradation of oleic and palmitic acids: Evidence of mass transfer limitations caused by long chain fatty acid accumulation onto the anaerobic sludge. Biotechnology and Bioengineering. 2005; 92:15-23. DOI: 10.1002/bit.20548
Angelidaki I, Ahring BK. Effects of free long-chain fatty acids on thermophilic anaerobic digestion. Applied Microbiology and Biotechnology. 1992; 37:808-812. DOI: 10.1007/bf00174850
Hwu CS, Donlon B, Lettinga G. Comparative toxicity of long-chain fatty acid to anaerobic sludges from various origins. Water Science and Technology. 1996; 34:351-358. DOI: 10.1016/0273-1223(96)00665-8
Lalman J, Bagley DM. Effects of C18 long chain fatty acids on glucose, butyrate and hydrogen degradation. Water Research. 2002; 36:3307-3313. DOI: 10.1016/s0043-1354(02)00014-3
Alves MM, Mota Vieira JA, Alvares Pereira RM, Pereira MA, Mota M. Effects of lipids and oleic acid on biomass development in anaerobic fixed-bed reactors. Part II: Oleic acid toxicity and biodegradability. Water Research. 2001; 35:264-270. DOI: 10.1016/S0043-1354(00)00242-6
Ma J, Zhao QB, Laurens LLM, Jarvis EE, Nagle NJ, Chen S, et al. Mechanism, kinetics and microbiology of inhibition caused by long-chain fatty acids in anaerobic digestion of algal biomass. Biotechnology for Biofuels. 2015; 8:141. DOI: 10.1186/s13068-015-0322-z
Chan PC, de Toledo RA, Iu HI, Shim H. Effect of zinc supplementation on biogas production and short/long chain fatty acids accumulation during anaerobic co-digestion of food waste and domestic wastewater. Waste and Biomass Valorization. 2018:1-11. DOI: 10.1007/s12649-018-0323-9
Wang CT, Yang CMJ, Chen ZS. Rumen microbial volatile fatty acids in relation to oxidation reduction potential and electricity generation from straw in microbial fuel cells. Biomass and Bioenergy. 2012; 37:318-329. DOI: 10.1016/j.biombioe. 2011.09.016
Oswald WJ, Golueke CG, Copper RC, Gee HK, Bronson JC. Water reclamation, algal production and methane fermentation in waste ponds. In: Advances in Water Pollution Research, Proceedings of the International Conference; September 1962; London. London: Pergamon Press LTD; 1964. pp. 119-157. DOI: 10.1016/B978-1-4832-8391-3.50029-4
Kong IC, Hubbard JS, Jones WJ. Metal-induced inhibition of anaerobic metabolism of volatile fatty acids and hydrogen. Applied Microbiology and Biotechnology. 1994; 42:396-402. DOI: 10.1007/BF00902748
Yenigün O, Kizilgün F, Yilmazer G. Inhibition effects of zinc and copper on volatile fatty acid production during anaerobic digestion. Environmental Technology. 1996; 17:1269-1274. DOI: 10.1080/09593331708616497
Osuna MB, Zandvoort MH, Iza JM, Lettinga G, Lens PNL. Effects of trace element addition on volatile fatty acid conversions in anaerobic granular sludge reactors. Environmental Technology. 2003; 24:573-587. DOI: 10.1080/09593330 309385592
Lee SJ. Relationship between oxidation reduction potential (ORP) and volatile fatty acid (VFA) production in the acid-phase anaerobic digestion process [thesis]. New Zealand: The University of Canterbury; 2008
Schmidt T, Nelles M, Scholwin F, Pröter J. Trace element supplementation in the biogas production from wheat stillage-optimization of metal dosing. Bioresource Technology. 2014; 168:80-85. DOI: 10.1016/j.biortech.2014.02.124
Fermoso FG, Collins G, Bartacek J, O’Flaherty V, Lens P. Role of nickel in high rate methanol degradation in anaerobic granular sludge bioreactors. Biodegradation. 2008; 19:725-737. DOI: 10.1007/s10532-008-9177-3
Fermoso FG, Collins G, Bartacek J, Lens PNL. Zinc deprivation of methanol fed anaerobic granular sludge bioreactors. Journal of Industrial Microbiology and Biotechnology. 2008; 35:543-557. DOI: 10.1007/s10295-008-0315-z
Paula LP, Bo J, Denise C, Alfons JMS, Gatze L. Effect of cobalt on the anaerobic thermophilic conversion of methanol. Biotechnology and Bioengineering. 2010; 85:434-441. DOI: 10.1002/bit.10876
Veeken A, Kalyuzhnyi S, Scharff H, Hamelers B. Effect of pH and VFA on hydrolysis of organic solid waste. Journal of Environmental Engineering. 2000; 126:1076-1081. DOI: 10.1061/(asce)0733-9372(2000)126:12(1076
Kavamura VN, Esposito E. Biotechnological strategies applied to the decontamination of soils polluted with heavy metals. Biotechnology Advances. 2010; 28:61-69. DOI: 10.1016/j.biotechadv.2009.09.002
Lin CY. Effect of heavy metals on volatile fatty acid degradation in anaerobic digestion. Water Research. 1992; 26:177-183. DOI: 10.1016/0043-1354(92)90217-r
Lin CY, Chou J, Lee YS. Heavy metal-affected degradation of butyric acid in anaerobic digestion. Bioresource Technology. 1998; 65:159-161. DOI: 10.1016/ s0960-8524(98)00022-4
Moonil K, Young-Ho A, Speece RE. Comparative process stability and efficiency of anaerobic digestion; mesophilic vs. thermophilic. Water Research. 2002; 36:4369-4385. DOI: 10.1016/s0043-1354(02)00147-1
White CJ, Stuckey DC. The influence of metal ion addition on the anaerobic treatment of high strength, soluble wastewaters. Environmental Technology. 2000; 21:1283-1292. DOI: 10.1080/09593332108618157
Bhattacharya SK, Qu M, Madura RL. Effects of nitrobenzene and zinc on acetate utilizing methanogens. Water Research. 1996; 30:3099-3105. DOI: 10.1016/s0043-1354(96)00194-7
Takashima M, Speece RE, Parkin GF. Mineral requirements for methane fermentation. Critical Reviews in Environmental Control. 1990; 19:465-479. DOI: 10.1080/10643389009388378
Zerkle AL, House CH, Brantley SL. Biogeochemical signatures through time as inferred from whole microbial genomes. American Journal of Science. 2005; 305:467-502. DOI: 10.2475/ajs.305.6-8.467
Shima S, Warkentin E, Thauer RK, Ermler U. Structure and function of enzymes involved in the methanogenic pathway utilizing carbon dioxide and molecular hydrogen. Journal of Bioscience and Bioengineering. 2002; 93:519-530. DOI: 10.1016/s1389-1723(02)80232-8
Bainotti AE, Nishio N. Growth kinetics of Acetobacteriumsp . On methanol-formate in continuous culture. Journal of Applied Microbiology. 2000; 88:191-201. DOI: 10.1046/j.1365-2672.2000.00854.x
Thauer RK, Kaster A, Goenrich M, Schick M, Hiromoto T, Shima S. Hydrogenases from Methanogenic Archaea, nickel, a novel cofactor, and H2 storage. Annual Review of Biochemistry. 2010; 79:507-536. DOI: 10.1146/annurev. biochem.030508.152103
Hoban DJ, BERG L. Effect of iron on conversion of acetic acid to methane during methanogenic fermentations. The Journal of Applied Bacteriology. 1979; 47:153-159. DOI: 10.1111/j.1365-2672.1979.tb01179.x
Rao PP, Seenayya G. Improvement of methanogenesis from cow dung and poultry litter waste digesters by addition of iron. World Journal of Microbiology and Biotechnology. 1994; 10:211-214. DOI: 10.1007/BF00360890
Ram MS, Singh L, Suryanarayana MVS, Alam SI. Effect of iron, nickel and cobalt on bacterial activity and dynamics during anaerobic oxidation of organic matter. Water, Air, and Soil Pollution. 2000; 117:305-312. DOI: 10.1023/A: 1005100924609
Pobeheim H, Munk B, Johansson J, Guebitz GM. Influence of trace elements on methane formation from a synthetic model substrate for maize silage. Bioresource Technology. 2010; 101:836-839. DOI: 10.1016/j.biortech.2009.08. 076
Qing-hao H, Xiu-fen L, He L, Guo-cheng D, Jian C. Enhancement of methane fermentation in the presence of Ni2+ chelators. Biochemical Engineering Journal. 2008; 38:98-104. DOI: 10.1016/j.bej.2007.07.002
Pobeheim H, Munk B, Lindorfer H, Guebitz GM. Impact of nickel and cobalt on biogas production and process stability during semi-continuous anaerobic fermentation of a model substrate for maize silage. Water Research. 2011; 45:781-787. DOI: 10.1016/j.watres.2010.09.001
Aresta M, Narracci M, Tommasi I. Influence of iron, nickel and cobalt on biogas production during the anaerobic fermentation of fresh residual biomass. Chemistry and Ecology. 2003; 19:451-459. DOI: 10.1080/02757540310001629134
Jain SK, Gujral GS, Jha NK, Vasudevan P. Production of biogas from Azolla pinnatar.Br and Lemna minorL.: Effect of heavy metal contamination. Bioresource Technology. 1992; 41:273-277. DOI: 10.1016/0960-8524(92)90013-N
Rother M. Selenoproteins in prokaryotes. In: Kretsinger RH, Uversky VN, Permyakov EA, editors. Encyclopedia of Metalloproteins. New York: Springer-Verlag; 2013. DOI: 10.1007/978-1-4614-1533-6_466
Michel R, Massanz C, Kostka S, Richter M, Fiebig K. Biochemical characterization of the 8-hydroxy-5-deazaflavin-reactive hydrogenase from Methanosarcina barkerifusaro. European Journal of Biochemistry. 1995; 233:727-735. DOI: 10.1111/j.1432-1033.1995.727_3.x
Hausinger RP. Nickel enzymes in microbes. The Science of the Total Environment. 1994; 148:157-166. DOI: 10.1016/0048-9697(94)90392-1
Zhu Z, Cheng G, Zhu Y, Zeng H, Wei R, Wei C. The effects of different anaerobic fermentation temperature on biogas fermentation of swine manure. In: 2011 International Conference on Computer Distributed Control and Intelligent Environmental Monitoring; 19-20 February 2011; Changsha. New York: IEEE; 2011. pp. 1410-1413. DOI: 10.1109/CDCIEM.2011.117