Research | Open | Published:
Physico-chemical pretreatment and fungal biotreatment for park wastes and cattle dung for biogas production
SpringerPlusvolume 4, Article number: 712 (2015)
With the rising demand for renewable energy and environmental protection, anaerobic digestion of biogas technology has attracted considerable attention within the scientific community. The effect of physico-chemical pretreatment on cellulose degradation followed by fungal treatment by Aspergillus terreus and Trichoderma viride to treat cellulosic biomass for enhancing its digestibility was investigated. The tested substrate was digested with and without physical, chemical, and biological treatment. Fresh leaves, dry leaves and cattle dung were characterized by a total solids content 35, 84 and 17 %, volatile solids content 81.2, 59.49 and 64.5 % and C/N ratio 31, 45.4 and 13.6, respectively. Biogas total volume was determined using water replacement technique, while methane volume was determined using precipitation of CO2 in 20 % NaOH solution. Pretreatment steps were carried out by using mechanical and chemical pretreatments using 2.5 % NaOH mixed with 2.5 % NH4OH for 15 days, followed by biological treatment of A. terreus and T. viride. The potential of pretreatment of substrate was studied at regular intervals of 0, 7, 14, 21, 28, 35, 42, 49, 56, 63 and 70 days determining the change in chemical and physical compositions of used substrates. Biogas production was 102.6 and 125.9 L/KgVS from untreated and pretreated substrate, respectively. On the other hand, methane production was 61.4 and 79.8 L/KgVS from untreated and pretreated substrate, respectively. In conclusion, Physical (milling), chemical (NaOH and NH4OH) pretreatment in addition to fungal (A. terreus and T. viride) treatment for the tested substrate prior to AD was an efficient process for improvement of biogas and methane production.
The consumption of renewable energy is dramatically increasing, along with energy security concerns, efforts to mitigate the environmental impact of conventional fuels, and improvements in living standards and renewable technologies. Bioenergy can play a central role in promoting renewable alternatives. In fact, bioenergy is estimated to be the fourth largest energy resource in the world (Chen and Lee 2014) due to its renewable and widely applicable characteristics and its abundance. Forestry resources, agricultural resources, sewage and industrial organic wastewater, municipal solid wastes, live-stock and poultry dung and biogas are major categories for use. Biogas, which is generally referring to gas from anaerobic digestion (AD) units, is a promising means of addressing global energy needs and providing multiple environmental benefits (Jiang et al. 2011). Biogas not only significantly reduces the costs of treating waste (Holm-Nielsen et al. 2009) but also has a relatively low feedstock cost. In addition, biogas has a lower sale price compared with diesel and petrol.
Biogas is generated from a digestion process under anaerobic conditions whose application is rapidly emerging as a viable means for providing continuous power generation. The AD cycle represents an integrated system of a physiological process of microbial and energy metabolism, as well as raw materials processing under specific conditions to produce biogas which is composed of methane and carbon dioxide and trace gases (Wu 2012). The pretreatment of wastes before AD is considered an effective method to improve biodegradability and biogas production from lignocellulosic materials by speeding up the hydrolysis step (Chen et al. 2005). Usual pretreatment methods including physical, chemical and biological may be used singly or in combinations (Sari and Budiyono 2014). Lignocellulose wastes mainly include crop residues and logging residues with crop residues making up the majority. For China, more than 800 million metric tons of waste agricultural straw is produced per year (Bi et al. 2009). However, this waste cannot be digested by itself due to recalcitrant materials (lignin, cellulose and hemi-cellulose) that result in low biodegradation and poor digestion performance; thus, extra accumulative measures are needed to start the digestive process such as pre-treatment and inoculums (Zhang et al. 2011).
Physical pretreatments were carried out to break down the cellular structure of biomass and to increase the specific surface area. This provided the chance for the lytic action of bacterial enzymes and reduction of viscosity in digesters, which is particularly important for cellulosic substrates (Schell and Harwood 1994). Chemical reagents are predominantly used for pretreatment of lignocelluloses materials due to their low-cost and high efficacy. By changing the properties of raw material, e.g., increasing the surface area, removing or dissolving lignin and hemicellulose, and reducing the crystallinity of cellulose, chemical reagents make lignocellulosic biomass more biodegradable and accessible to anaerobic microorganisms (Sun et al. 2014; Mao et al. 2015).
Microbiological pretreatment can speed up the degradation rate of substrates in anaerobic digestion. Bacterial and fungal cellulose-, hemicellulose- and starch-degrading enzymes are responsible for enhancing the substrate digestibility (Muñoz et al. 2014). However, the microbial community is sensitive to variations in the operating conditions applied. Thus, the AD process, if improperly managed, would become unstable and result in reduced biogas production. Although previous studies have discussed AD development, most focused on only one aspect (such as technology, mechanism, factors affecting efficiency, etc.) to minimize this instability (Munk et al. 2010) or on one substrate (such as livestock manure, urban solid waste, food waste, crop straw, etc.). Fungi, particularly those that attack lignin, are mainly used in the pretreatment of lignocellulosic biomass for biogas production. Several fungi classes, including brown-rot, white-rot and soft-rot fungi (i.e., Ceriporiopsis subvermispora, Auricularia auricula-judae, Trichoderma reesei), and basidiomycetes (e.g., Ischnoderma resinosum and Fomitella fraxinea) have been used for pretreatment with white-rot fungi being the most effective through the action of lignin-degrading enzymes (e.g., peroxidases and laccase) (Zheng et al. 2014). After fungal pretreatment, a 5–15 % increase in the methane yield was obtained (Mackuľak et al. 2012; Sun et al. 2014). The aim of this study is to improve the performance of anaerobic digestion of lignocellulosic park wastes and cattle dung, by applying physico-chemical pretreatments and fungal fungal treatment. In addition, daily and cumulative production of biogas, CH4 and CO2 is evaluated for both untreated and pretreated. Beside, study of the changes in different parameters that control the anaerobic digestion process.
Procurement of the materials
Samples of Park wastes (fresh and dry leaves) were collected from Faculty of Science at Tanta University parks. The fresh and dried leaves were chopped to 3–4 cm and were stored in polythene bags at room temperature. Cattle dung sample of the various microbial inocula for AD had been collected from a farm at El-Hamrawy village in Kafr El-Sheikh Governorate, Egypt and placed in sealed plastic bags and then frozen at −20 °C, to retain microbial viability in the collected sample (Williams and Withers 2012).
Before mixing with cattle dung, mechanical pretreatment was performed on the collected park wastes (fresh and dried leaves), by using a cutting mill and then sieved with 2 mm screen (Bochmann and Montgomery 2013) In order to achieve a squeezing for the cellular structure of park wastes for the pretreatment prior to anaerobic digestion.
Lignocellulosic materials are resistant to hydrolysis due to their structure and composition. Alkali addition causes swelling of lignocelluloses and partial lignin solubilisation (Kong et al., 1992). Park wastes were soaked in combination of 2.5 % NaOH and 2.5 % NH4OH for 15 days in a closed plastic container to improve delignification levels (Elumalai et al. 2014). After chemical pretreatment step, pH was adjusted using dilute 1 N HCl to achieve a suitable medium for the biological pretreatment and fungal growth (Alvarez et al. 2013).
Isolation and identification of fungi
Fungi were isolated from an old digester slurry (cattle dung and food waste mixture) using a tenfold serial dilution-plating technique on potato dextrose agar (PDA) plates into which 30 µg of chloramphenicol was added. The plates were incubated at 25 °C. The cultures were observed daily and fungal growth was subcultured onto fresh PDA plates until pure isolates were obtained. The plates were identified macroscopically and microscopically using colony color, type, texture, shape and growth pattern according to the detailed drawing of the features and identification manual and guides of Gilman (1959), Booth (1971), Moubasher (1993) and Blackwell (2011). The isolated fungi were maintained on potato dextrose agar (PDA) slant and stored at 4 °C.
Preparation of inocula
Inoculum suspensions were prepared from fresh, mature cultures grown on PDA and Sabouraud agar. The colonies were covered with 5 mL of distilled water. Tween 20 (5 %) was added to facilitate inoculum preparation. The mixture was collected in a sterile tube with vortexing for 15 s (Petrikkou et al. 2001).
Preparation of starter culture
In order to obtain biogas and methane production, the method of Maramba (1978) was employed. Cattle dung, which is well known to contain methanogenic consortia, will be used to start the inoculation of the digester. The starter material was prepared 20 days before the start of charging fresh substrate in the digester. A volume of 500 mL of starter was prepared at 1:1 ratio (water to cattle dung) and placed in a closed plastic bottle connected with a submerged tube, so all the gas can come out without air entrance to the drum.
Two digesters each contained a mixture of 125 g of fresh leaves, 125 g of dried leaves and 250 g of cattle dung. The substrate in the first digester was milled to 2 mm then pretreated with alkaline solution (2.5 % NaOH mixed with 2.5 % NH4OH) and the pH was adjusted by using diluted 1 N HCl to be a suitable medium (pH 7.1) for biological treatment by two isolated and identified fungi (Aspergillus terreus and Trichoderma viride) isolated from the old digester slurry. The second digester was left without any pretreatment as a control. Fungal treatment of park wastes was kept at 25 °C for 7 days followed by incubation of the both digesters for 70 days on incubator shaker (35 °C, 120 rpm) to assist in the mixing process as shown in Fig. 1. Physico-chemical analyses samples were collected from effluent outlet at the bottom of the digester at regular intervals of 0, 7, 14, 21, 28, 35, 42, 49, 56, 63 and 70 to determine pH, EC and C/N ratio.
Biogas, methane and carbon dioxide volume
Daily methane volume was determined using a system developed in our laboratory of Microbiology at Faculty of Science, Tanta University. The system consists of four units connected together using connecting pipelines, as shown in Fig. 1. The first unit contains a simple designed batch plastic digester equipped with biogas outlet, solid sample outlet, thermometer and valve spout effluent outlet. The second unit is an application for water replacement technique which is used to measure total volume of biogas. Ergüder et al. (2000) reported that the gas production in batch reactors was determined by a water displacement device. The third unit used to determine the volume of methane and carbon dioxide gases by passing produced biogas in 20 % NaOH. After biogas elevation, the container shaken and left for 30 min to measure the methane volume according to (Manilla et al. 2001) and Wojciech (2012) who reported that sodium hydroxide (NaOH) reacts with carbon dioxide (CO2) through chemical processes. When the produced biogas passes through sodium hydroxide, sodium bicarbonate (NaHCO3) is formed according to Eq. (1). In this way, carbon dioxide and water moisture were removed from the entire gas.
The content of CH4 in biogas was determined as follows: A known volume of the headspace gas was produced in a two liter container to determine the total volume of biogas by water replacement technique (VB), and it was injected into another container which contained 20 % NaOH solution. This container was shaken manually for 3–4 min so that all the CO2 could be absorbed in the concentrated NaOH solution, then it was left for 30 min. The volume of remaining gas (VM) refers to the produced methane volume. Hence, the volume of methane and carbon dioxide (VC) can be calculated according to Eq. (2) (Ergüder et al. 2000; Tippayawong and Thanompongchart 2010; Drosg et al. 2013).
The fourth unit used to collect and store all purified methane gas.
The physico-chemical properties of park wastes before and through anaerobic digestion process were implemented at Ministry of Agriculture and land reclamation laboratories in Gharbia in addition to Kafr El-Sheikh University central laboratory of environmental studies (KUCLES).
Total solids (TS) and volatile solids (VS)
Analyses of samples were carried out using APHA standard methods (APHA 1995) by taking a known weigh of sample in dried aluminum container. At the beginning, the weight of empty containers alone and containers with samples together was determined. The containers were placed in a furnace at 105 °C for 12 h to evaporate water for total solids (TS) calculation. Weight of the containers was determined. For volatile solids (VS) calculations, the contents were put in another furnace at 550 °C for 3 h. The weight was then recorded. Mathematical formulas for TS and the VS calculation are shown below. Organic matter (OM) is the percentage of VS/TS.
A: weight of dried sample after 12 h at 105 °C, B: weight of container, C: weight of wet sample, D: weight of burnt sample after 3 h at 550 °C.
A mass of 10 g of digester slurry was added to a sample cup. The sample was mixed with water (1:1 v/v). The slurry allowed setting, after vigorous stirring, for 1 h at room temperature. Then pH was measured by pH meter (Miller and Kissel 2010).
Electric conductivity (EC)
A weight of 5 g air dried sample was dissolved in 50 mL distilled water (1:10 w/v) and shaken on an orbital shaker for 40 min. Then supernatant was taken and EC of the supernatant was recorded using a pen type Total dissolved solids (TDS) meter (Peters et al. 2003). The results were expressed in dSm−1 according to Eq. 5.
Total organic carbon (TOC)
Total organic carbon in the tested substrates was determined according to Page et al. (1982) by multiplying Organic matter percentage in 0.58.
Total Kjeldah nitrogen (TKN)
For determination of organic and the inorganic forms of nitrogen, Total Kjeldahl Nitrogen (TKN) was analyzed by kjeldahl digestion method (APHA 1992). The substrate sample (1 g) was digested at 400 °C for 60–90 min. by adding 12 mL of concentrated sulphuric acid. For raising the boiling point, 3.5 g potassium sulfate (K2SO4) was added. In addition to 0.4 g of copper sulfate (CuSO4) was added as a catalyst. The tubes are left to cool off until the disappearance of white fumes. Subsequently, 50 ml sodium hydroxide was automatically added to the sample for convert NH4 + to NH3. The sample was distilled and condensed into 10 mL of boric acid solution, and the content was determined by acid–base titration. The titration endpoint was situated around pH 5.3 with color change visualization from green to blue/purple and by addition of methyl red methylene blue indicator.
Results are presented as the mean ± standard deviation (SD) from three replicates. The statistical analyses were carried out using SAS (v 6. 12). Data obtained were analyzed statistically to determine the degree of significance using one way analysis of variance (ANOVA) and t test at probability level p ≤ 0.05.
As shown in Additional file 1: Table S1, the park wastes (fresh and dry leaves) and cattle dung characterization revealed that the dried leaves had the highest TS content (84 %) and the highest value of C/N (45.4). On the other hand, cattle dung had low TS content and C/N ratio representing 17 % and 13.6, respectively. Fresh leaves contained the highest VS and TOC representing 81.2 % and 47.1 %, respectively. The highest percentage of TNK was recorded for cattle dung (2.8 %).
Biogas and methane production
The optimization conditions for biogas and methane production from the used substrate were investigated through two pretreatment processes including physical (milling) and chemical (2.5 % NaOH mixed with 2.5 % NH4OH for 15 days) followed by fungal treatment using Aspergillus terreus and Trichoderma viride for 7 days. Biogas production and process parameters were recorded during 70 days of retention time.
Biogas and CH4 yields of the pretreated and untreated substrate were measured. The daily and accumulative productions of biogas and CH4 obtained during 70 days of digestion from untreated and pretreated substrate were shown in Additional file 1: Table S2 and in Figs. 2 and 3. Daily biogas and CH4 production yields from the substrate were improved by the three pretreatment stages. The highest biogas and CH4 yield of 2.6 and 1.9 L/KgVS, respectively was obtained from pretreated substrate in the 28th day compared to untreated substrate. On the other hand, the cumulative production of biogas for untreated substrate was 102.6 L/KgVS which elevated to 125.9 L/KgVS in case of pretreated substrate which showed 22.7 % improvement compared to the biogas yield from untreated substrate. Cumulative CH4 production of pretreated and untreated substrate was 79.8 and 61.4 L/KgVS, respectively with 30 % improvement compared to the methane yield from untreated substrate. CO2 showed a reduction rate after pretreatment quantified by 11.9 %.
Statistical analysis of biogas, methane and CO2 production of untreated and pretreated substrate was shown in Additional file 1: Table S2. Substrate pretreatment had a significant improvement effect on the biogas and methane production after the 14th day; while being insignificant to that till the 56th day, and this showed the stability in the biogas and methane production through AD period. Beside, CO2 production showed significant decreasing values after 14th day and insignificant decrease from the 28th till 56th day.
pH, EC and C/N
Insignificant decrease in pH values of untreated substrate till the 2nd week of AD followed by significant decreasing till the 8th week. An increase in pH values was observed again at the beginning of the 8th week till the 10th week for both untreated and pretreated substrate. The changes in Electric conductivity (EC) of untreated substrate were observed (2.6–3.7 dSm−1) and showed directly proportional increasing along with the retention time. Moreover, EC values from the substrate were improved by its pretreatment (3.2–4.6 dSm−1). Statistical analysis showed significant changes in EC for both untreated and pretreated substrate. However, insignificant increase from the 56th day till the 70th day was recorded for the pretreated substrate. Additional file 1: Table S3 and Fig. 4, represented a significant change in C/N ratio during AD process for 70 days. Pretreatment of the substrate improved C/N in the first day to be 26.1 compared to untreated substrate (28.8), and decreased to be 12.3 at the end of AD time for pretreated substrate. In the same concern, a significant decreasing in C/N for untreated substrate was observed through the period of retention time to be 18 at the end of AD time.
Lignocelluloses are basically composed of carbohydrates (cellulose and hemicelluloses), lignin, and extraneous materials (Karimi et al. 2013). However, the compact crystalline structure where lignin physically protects the cellulose and hemicelluloses parts makes these materials more resistant to anaerobic digestion (Mosier et al. 2005). In the anaerobic digestion process, if a substrate is well enclosed in lignin structures, the type of disintegration of the substrate becomes important. The structure should be disrupted or defibrated rather than cut, because they are refractory to decomposition under anaerobic conditions (Pesta 2007). Without prior treatments, a slow hydrolysis might occur and biogas production could become low with a long retention time required to produce sufficient amount of biogas (Yu and Schanbacher 2010). In the present study, the used substrate was soaked in alkaline solution (2.5 % NaOH mixed with 2.5 % NH4OH) followed by fungal treatment for 7 days. Zuo et al. (2012) showed that a novel soaking pretreatment (NaOH and aqueous-ammonia) for corn stover was developed to remove lignin, swell the biomass, and improve enzymatic digestibility. Furthermore, alkalis help prevent decreases in pH during the acidogenesis process and increasing the efficiency of methanogenesis (Mao et al. 2015). Taherzadeh and Karimi (2008) showed that in alkaline pretreatment the biomass is soaked by alkaline solution at relatively low temperature for a certain amount of time. Zhang et al. (2011) compared the results of biogas production from corn straw which was subjected to 8 % NaOH, 5 % ammonia and 4 % urea pre-treatments at an ambient temperature for 20 days prior to anaerobic digestion. He et al. (2008) showed a significant increase in biogas yield in batch tests using rice straw pretreated with 6 % solid NaOH for 3 weeks at ambient temperature. Ghosh and Bhattacharyya (1999) studied white-rot fungi and reported their ability on complete lignin degradation, and their application has been suggested for partial delignification to increase digestibility. In the same concern, Song et al. (2013) reported that the pretreatment with white-rot fungi can effectively remove lignin and decompose the biomass structure to enhance subsequent enzymatic hydrolysis. As well as, alkali pretreatment led to delignification of lignocellulosic fibers and the substrate became easier to be biodegraded. Sambusiti et al. (2012) reported that recombination of different pretreatment methods led to a solubilization of holocellulose and lignin. Ishola et al. (2014) indicated the ability of recombination between physical, chemical and biological pretreatments to degrade cellulosic biomass and increase its digestibility and its effect on biogas and methane production.
In the current study, the methane yield was enhanced by 30 % after the use of fungal (A. terreus and T. viride) and alkaline pretreatment (2.5 % NaOH mixed with 2.5 % NH4OH). Thus, the pretreatment used in this work was effective compared to Liew et al. (2011) who showed that the methane yield increased by 20 % using 3.5 % NaOH on fallen leaves. Zheng et al. (2009) and Yu et al. (2014) reported that the simultaneous alkaline treatment not only helped to improve the digestibility of park wastes but also increased the buffering capacity of the digester to maintain suitable pH, thus leading to significant increase in biogas and methane yield compared with no or low alkaline loadings. The biological pretreatment has been extensively studied due to its several advantages, such as non-toxicity, environmental friendly, no chemical requirement, mild environmental conditions and low energy requirements. However, long pretreatment time is needed because the rate of the biological hydrolysis is usually very low, which is the main disadvantage of biological pretreatment methods (Taherzadeh and Karimi 2008). The obtained results revealed the improved biogas production (22.7 %) by chemically and biologically substrate pretreatment (125.9 L/KgVS) compared to untreated substrate (102.6 L/KgVS). In addition, CH4 production of pretreated substrate (79.8 L/KgVS) was improved than untreated one (61.4 L/KgVS) by 30 %. On the other hand, carbon dioxide production was reduced by 11.9 % after pretreatment. The present study showed the changes in pH values of untreated substrate from 7.1 to 7.5 after 70 days, and from 7.5 to 7.8 for pretreated substrate. The pH value of the AD substratum influences the growth of methanogenic microorganisms and the dissociation of some compounds relevant for the AD process, i.e. ammonia, hydrogen sulphide and organic acids (Al Seadi et al. 2008). Methane formation takes place within a relatively narrow pH range, between 5.5 and 8.5 ca., with an optimal range of between 7.0 and 8.0 for most methanogens (Al Seadi et al. 2008). Ho et al. (2013) stated that the drop occurred in pH values was due to the formation of volatile fatty acids after anaerobic digestion process, which caused a drop in pH value to turn the conditions favourable to methanogenic bacteria which consumed acetic acid and raise pH value again. Moreover, EC values of untreated substrate varied from 2.6 to 3.7 dSm−1. However, in pretreated substrate EC reached to 4.6 dSm−1 by the end of anaerobic digestion. The gradual increase in EC values might be due to high concentration of nutrient ions released during the organic matter mineralization. Bakili et al. (2014) and Okoroigwe et al. (2014) reported that the C/N ratio must range from 20 to 30 to make a nutritional balance for microorganisms inside the digester. The current results showed that the C/N ratio changed from 28.8 (untreated substrate) to 26.1 after physical, chemical pretreatment in addition to fungal (A. terreus and T. viride) treatment, revealing the effect of these pretreatment steps in improvement of C/N ratio. The C/N ratio of untreated and pretreated substrate showed a gradual decrease C/N values along with retention time due to bacterial activity that consumes total organic carbon as well as using a small amount of nitrogen (Tchobanoglous et al. 1993). The content of organic matter and organic carbon decreased because of the physico-chemical pretreatment and fungal activities which can degrade cellulose and lignin and hence increase biogas production. Weiland (2010) reported that a ratio of around 30 is favourable for microbial cell metabolism. But lower C/N ratio than 10–15 leads to ammonium releasing and inhibition of bacterial growth. This explains, in the present study, the decreasing of biogas production after lowering C/N ratio through anaerobic digestion. This decreasing in C/N ratio may affect methanogenic bacteria and thus decreasing in methane yield.
Physical (milling), chemical (NaOH and NH4OH) pretreatment in addition to fungal (A. terreus and T. viride) treatment for park wastes and cattle dung substrate prior to AD was an efficient process for improvement of biogas and methane production. Moreover, further work is needed to ensure that the recycling of treated and untreated lignocellulosic wastes results in the improvement of agriculture.
Al Seadi T, Rutz D, Prassl H, Köttner M, Finsterwalder T, Volk S, Janssen R (2008) Biogas Handbook. University of Southern Denmark Esbjerg, Esbjerg, pp 9–10
Alvarez CES, Miranda JL, Castro MR, Verdín GP, Pérez MAR, Hernández IC (2013) Alkaline pretreatment of Mexican pine residues for bioethanol production. Afr J Biotechnol 12(31):4956–4965
APHA (1992) Standard methods for the examination of water and wastewater, 18th edn. American Public Health Association, Washington
APHA (1995) Standard methods for the examination of water and wastewater, 19th edn. American Public Health Association, Washington
Bakili S, Gessesse A, Mtei K, Njau K (2014) Anaerobic digestion of banana winery effluent for biogas production. Int J Environ Prot Polic 2(5):168–173
Bi Y, Gao C, Wang Y, Li B (2009) Estimation of straw resources in China. Trans Chin Soc Agric Eng 25:211–217
Blackwell M (2011) The Fungi: 1, 2, 3… 5.1 million species? Am J Bot 98(3):426–438
Bochmann G, Montgomery LFR (2013) Storage and pre-treatment of substrates for biogas production. In: Wellinger A, Murphy JD, Baxter D (eds) The biogas handbook: Science, production and applications. Woodhead Publishing Limited, Cambridge (ISBN 978 0 85709 498 8)
Booth C (1971) The genus Fusarium, 1st edn. Commonwealth Mycological Institute, Kew Surrey, p 237
Chen HH, Lee AHI (2014) Comprehensive overview of renewable energy develop-ment in Taiwan. Renew Sustain Energy Rev 37:215–228
Chen H, Liu L, Yang Z, Li Z (2005) New process of Maize stalk amination treatment by steam explosion. Biomass Bioenerg 28:411–417
Drosg B, Alsaedi T, Braun R, Bochmann G (2013) Analysis and characterisation of biogas feedstocks. In: Wellinger A, Murphy JD, Baxter D (eds) The biogas handbook: science, production and applications. Woodhead Publishing Limited, Cambridge, UK
Elumalai S, Roa-Espinosa A, Markley JL, Runge TM (2014) Combined sodium hydroxide and ammonium hydroxide pretreatment of post-biogas digestion dairy manure fiber for cost effective cellulosic bioethanol production. Sustain Chem Process 2:12. doi:10.1186/2043-7129-2-12
Ergüder TH, Güven E, Demirer GN (2000) Anaerobic treatment of olive mill wastes in batch reactors. Process Biochem 36:243–248
Ghosh A, Bhattacharyya BC (1999) Biomethanation of white rotted and brown rotted rice straw. Bioprocess Eng 20:297–302
Gilman J (1959) A manual of soil fungi. The Iowa state University Press, Ames
He Y, Pang Y, Liu Y, Li X, Wang K (2008) Physicochemical characterization of rice straw pretreated with sodium hydroxide in the solid state for enhancing biogas production. Energ Fuel 22:2775–2781
Ho DP, Jensen PD, Batstone DJ (2013) Methanosarcinaceae and acetate oxidizing pathways dominate in high-rate thermophilic anaerobic digestion of waste activated sludge. Appl Environ Microbiol 79(20):6491–6500
Holm-Nielsen JB, Al Seadi T, Oleskowicz-Popiel P (2009) The future of anaerobic digestion and biogas utilization. Bioresour Technol 100:5478–5484
Ishola M, Isroi B, Taherzadeh M (2014) Effect of fungal and phoshoric acid pretreatment on ethanol production from oil palm empty fruit bunches. Bioresour Technol 165:9–12. doi:10.1016/j.biortech.2014.02.053
Jiang X, Sommer SG, Christensen KV (2011) A review of the biogas industry in China. Energy Polic 39:6073–6081
Karimi K, Shafiei M, Kumar R (2013) Progress in physical and chemical pretreatment of lignocellulosic biomass. In: Gupta VK, Tuohy MG (eds) Biofuel technologies. Springer, Berlin, pp 53–96
Kong F, Engler C, Soltes E (1992) Effects of cell-wall acetate, xylan backbone and lignin on enzymatic hydrolysis of aspen wood. Appl Biochem Biotechnol 34–35:23–35
Liew LN, Shi J, Li Y (2011) Enhancing the solid-state anaerobic digestion of fallen leaves through simultaneous alkaline treatment. Bioresour Technol 102:8828–8834
Mackuľak T, Prousek J, Švorc Ľ, Drtil M (2012) Increase of biogas production from pretreated hay and leaves using wood-rotting fungi. Chem Pap 66:649–653
Manilla PN, Ogali RE, Uzoukwu BA (2001) Undergraduate chemistry fundamental principles. Timi Hyacinth Enterprises, Lagos
Mao C, Feng Y, Wang X, Ren G (2015) Review on research achievements of biogas from anaerobic digestion. Renew Sustain Energy Rev 45:540–555
Maramba FD (1978) Biogas and waste recycling: the Philippine experience: Maya farms division. Liberty Flour Mills Inc, Philippines
Miller RO, Kissel DE (2010) Comparison of soil pH methods onsoils of North America. Soil Sci Soc Am J 74:310–316
Mosier N, Wyman C, Dale B, Elander R, Lee YY, Holtzapple M et al (2005) Features of promising technologies for pretreatment of lignocellulosic biomass. Bioresour Technol 96:673–686
Moubasher AH (1993) Soil fungi in Qatar and other Arab countries. The Scientific and Applied Research Center, University of Qatar, Doha, p 566
Munk B, Bauer C, Gronauer A, Lebuhn M (2010) Population dynamics of methano-gens during acidification of biogas fermenters fed with maize silage. Eng Life Sci 10:496–508
Muñoz C, Hidalgo C, Zapata M, Jeison D, Riquelme C, Rivas M (2014) Use of Cellulolytic Marine Bacteria for Enzymatic Pretreatment in Microalgal Biogas Production. Appl Environ Microbiol 80:4199–4206. doi:10.1128/AEM.00827-14
Okoroigwe EC, Ibeto CN, Ezema CG (2014) Experimental study of anaerobic digestion of dog waste. Sci Res Essays 9(6):121–127
Page AL, Miller RH, Keeney DR (1982) Methods of Soil Analysis, 2nd edn. Amercen Society of Agronomy, Madison
Pesta G (2007) Anaerobic digestion of organic residues and wastes. In: Oreopoulou V, Russ W (eds) Utilization of by-products and treatment of waste in the food industry. Springer, New York, pp 53–72
Peters J, Combs SM, Hoskins B, Jarman J, Kovar JL, Watson ME, Wolf AM, Wolf N (2003) Recommended methods of manure analysis (A3769). University of Wisconsin Extension. http://www1.uwex.edu/ces/pubs
Petrikkou E, Rodriguez-Tudela JL, Cuenca-Estrella M, Gomez A, Molleja A, Mellado E (2001) Inoculum standardization for antifungal susceptibility testing of filamentous fungi pathogenic for humans. J Clin Microbiol 39:1345–1347
Sambusiti C, Ficara E, canziani R (2012) Physical, chemical and biological pretreatments to enhance biogas production from lignocellulosic substrates. Ph D Thesis, DICA (Department of Civil and Environmental Engineering), politecnico di Milano University, Italy
Sari FP, Budiyono B (2014) Enhanced biogas production from rice straw with various pretreatment : a review. Waste technol 2(1):17–25
Schell D, Harwood C (1994) Milling of lignocellulosic biomass. Appl Biochem Biotechnol 45–46(1):159–168. doi:10.1007/BF02941795
Song Z, Yang G, Han X, Feng Y, Ren G (2013) Optimization of the alkaline pretreatment of rice straw for enhanced methane yield. BioMed Research International, (Article ID 968692)
Sun JZ, Ding SY, Peterson DJ (2014) Biological conversion of biomass for fuels and chemicals—explorations from natural biomass utilization systems. The RSC energy & environment. Royal Society of Chemistry (RSC), London (ISBN: 978-1-84973-424-0)
Taherzadeh MJ, Karimi K (2008) Pretreatment of lignocellulosic wastes to improve ethanol and biogas production: a review. Int J Mol Sci 9(9):1621–1651
Tchobanoglous G, Theisen H, Vigil SA (1993) Integrated solid waste management: engineering principles and management issues, 2nd edn. McGraw-Hill International, New York, p 978 (ISBN-13: 9780070632370)
Tippayawong N, Thanompongchart P (2010) Biogas quality upgrade by simultaneous removal of CO2 and H2S in a packed column reactor. Energy 35(12):4531–4535
Weiland P (2010) Biogas production: current state and perspectives. Appl Microbiol Biot 85(4):849–860
Williams AG, Withers S (2012) Sutherland AD: The potential of bacteria isolated from ruminal contents of seaweed-eating north ronaldsay sheep to hydrolyse seaweed components and produce methane by anaerobic digestion in vitro. Microbial Biotechnol 6(1):45–52
Wojciech MB (2012) Benefits of biogas upgrading to biomethane by high-pressure reactive solvent scrubbing. Biofpr 6:12–20
Wu B (2012) Integration of mixing, heat transfer, and biochemical reaction kinetics in anaerobic methane fermentation. Biotechnol Bioeng 109(11):2864–2874. doi:10.1002/bit.24551
Yu Z, Schanbacher F (2010) Production of methane biogas as fuel through anaerobic digestion. In: Singh OV, Harvey SP (eds) Sustainable biotechnology. Springer, Netherlands, pp 105–127
Yu L, Bule M, Ma J, Zhao Q, Frear C, Chen S (2014) Enhancing volatile fatty acid (VFA) and bio-methane production from lawn grass with pretreatment. Bioresource Technol 162:243–249
Zhang L, Lee Y-W, Jahng D (2011) Anaerobic co-digestion of food waste and piggery wastewater: focusing on the role of trace elements. Bioresour Technol 102:5048–5059
Zheng MX, Li XJ, Li LQ, Yang XJ, He YF (2009) Enhancing anaerobic biogasification of corn stover through wet state NaOH pretreatment. Bioresour Technol 100(21):5140–5145
Zheng Y, Zhao J, Xu F, Li Y (2014) Pretreatment of lignocellulosic biomass for enhanced biogas production. Prog Energy Combust Sci 42:35–53
Zuo Z, Tian S, Chen Z, Li J, Yang X (2012) Soaking pretreatment of corn stover for bioethanol production followed by anaerobic process. Appl Biochem Biotechno 167:2088–2102
SSA have been involved in the design of the study, isolation and identification of fungi, experiment set up, collecting data, writing, drafting and revising the manuscript and JZS revised the manuscript critically for important intellectual content. Both authors read and approved the final manuscript.
The authors like to thank Dr. Abd El-Fatah Abomohra (Botany Department, Faculty of Science, Tanta University, Egypt) for helping with statistical analysis for the given data and to Mr. Tamer S. El-Samahy for his assistance in collection of the samples. This work was funded by Egyptian Ministry of Higher Education and Scientific Research (MHESR), Supporting of Excellence Students Projects (SESP).
The authors declare that they have no competing interests.