Production of humic substances through coal-solubilizing bacteria

RESEARCH PAPER

Production of humic substances through coal-solubilizing bacteria

Nelson Valero^{I, II}; Liliana Gómez^I; Manuel Pantoja^I; Ramiro Ramírez^III

^ILaboratory of Environmental and Agricultural Microbiology, Universidad Popular del Cesar, Campus Sabanas, Valledupar, Colombia

^IIFaculty of Basic Science, Universidad de La Guajira, Riohacha, Colombia

^IIISoil Physics Laboratory, Universidad Nacional de Colombia, Medellín, Colombia

^{Correspondence}

ABSTRACT

In this paper, the production of humic substances (HS) through the bacterial solubilization of low rank coal (LRC) was evaluated. The evaluation was carried out by 19 bacterial strains isolated in microenvironments with high contents of coal wastes. The biotransformed LRC and the HS produced were quantified in vitro in a liquid growth medium. The humic acids (HA) obtained from the most active bacterial strain were characterized via elemental composition (C, H, N, O), IR analyses, and the E₄/E₆ ratio; they were then compared with the HA extracted chemically using NaOH. There was LRC biotransformation ranged from 25 to 37%, and HS production ranged from 127 to 3100 mg.L^-1. More activity was detected in the isolated strains of Bacillus mycoides, Microbacterium sp, Acinetobacter sp, and Enterobacter aerogenes. The HA produced by B. mycoides had an IR spectrum and an E₄/E₆ ratio similar to those of the HA extracted with NAOH, but their elemental composition and their degree of aromatic condensation was different_. Results suggest that these bacteria can be used to exploit the LRC resulting from coal mining activities and thus produce HS in order to improve the content of humified organic matter in soils.

Key words: low rank coal, Microbacterium sp, Bacillus mycoides, Acinetobacter baumannii, Enterobacter aerogenes.

Introduction

Humic substances (HS) are considered large supramolecular arrays resulting from the self-assembling of relatively small heterogeneous humic molecules derived from the degradation of biological materials. These supramolecular associations are stabilized by hydrogen bridges and weak hydrophobic bonds such as the Van der Waals forces, π-π, and CH-π (Piccolo 2002). The HS in the soil play an important role in physical and chemical quality, carbon capture and stabilization (Piccolo et al., 2004), and in the inactivation of pesticides, heavy metals, and other polluting agents (Bandeira et al., 2009). HS also stimulate plant physiology (Badis et al., 2009), induce root proliferation, and modify the architecture of the root system (Barros et al., 2010). As a result of this, HS stimulate plant growth and development (Trevisan et al., 2010).

Currently, HS are commonly used as organic amendments for agricultural soils. Low rank coals (LRC) such as peat, leonardite, and lignites are not exploited commercially due to their low energetic power. However, they are considered a HS-rich source. To obtain HS from this source, the classical method, i.e. extraction using alkaline solutions, is used (Senesi et al., 2007; Chassapis and Roulia, 2008). Nevertheless, there is increased interest in solubilizing coal through the ligninolytic microorganisms in the soil as an alternative procedure to obtain HS.The coal solubilization processes that have been studied in greater detail include the basidiomycetes fungi involved in wood rotting processes. These fungi are: Trametes versicolor (Ralph and Catchside, 1996), Nematoloma frowardii (Hofrichter and Fritsche, 1997), and Phanerochaete chrysosporium (Ralph and Catchside, 1997). Likewise, saprophytic soil fungi such as Trichoderma atroviridae (Holker and Hofer, 2002; Oboirien et al., 2008) and Penicillium decumbens (Yin et al., 2009) have also been studied.

Despite the advances in the understanding of the microbial transformation of coal, it is still not possible to develop efficient and economically viable biotechnological processes to produce HS by solubilizing LRC with fungi. The main reason is the difficulty in handling coal in bioreactors and the loss of process stability due to a complex regulation of the solubilization mechanisms. Furthermore, the main mechanism for coal solubilization through fungi is the production of ligninolytic enzymes (Willman and Fakousa, 1997; Gockay et al., 2001); however, it is often observed that depolymerization of the released HS takes place after coal solubilization (Hofrichter and Fritsche, 1997). This phenomenon has been associated with the activity of the laccase (Fakousa and Hofrichter, 1999; Ralph and Catcheside, 1998; Zaavarzinda et al., 2004), lignin peroxidase (Ralph and Catcheside, 1998b), and manganeso peroxidase enzymes (Hofrichter 2002). This depolymerization of HS leads to loss of their supramolecular conformation and consequently reduces their effect on soil properties and their bioactivity on plants.

There is another procedure for solubilizing coal that does not rely on fungi: coal solubilization through bacteria. This process uses non-enzymatic mechanisms such as the production of surfactants, chelators, and alkaline substances (Hofrichter and Fakoussa, 2004). Therefore this may be an alternative to prevent the depolymerization of the HS produced. There are studies on bacterial solubilization of coal through Escherichia freundii, Pseudomonas rathonis, Pseudomonas fluorescens, Streptomyces setoni, (Laborta et al., 1997); Pseudomonas putida (Machnikouska et al., 2002), Rhodococcus spp (Fuchtenbusch and Steinbuchel, 1999), Bacillus, Rhodococcus, and Staphylococcus (Pokorny et al., 2005), as well as through the actinomycetes Streptomyces setonii (Willman and Fakoussa, 1997) and Streptomyces viridosporous (Strandberg and Lewis, 1987). Recent studies have described the role that the actinomycetes with ligninolytic activity play in the regulation of the polymerization of HS in the soil. (Badis et al., 2009).

This study aimed to evaluate the solubilization of LRC derived from hard coal mining activities in the "El Cerrejón" open cast mine (La Guajira, Colombia).The goal was to analyze the production of HS due to the activity of native bacteria isolated from microenvironments with high contents of coal waste. This study seeks to advance in the development of a strategy for use or final disposal of LRC directly on the soil by means of bioaugmentation with coal solubilizing bacteria to provide humified organic matter for use in land reclamation processes after mining activities, or for degraded soil due to organic matter loss.

Materials and Methods

Microorganisms: 19 bacteria strains were selected, which were isolated from soil mixed with coal residues, coal sediment resulting from coal washing, and the rhizosphere of Cenchrus ciliaris and Typha domingensis, two plants from the gramineae family which grow on soil and sediments with high amounts of coal particles in areas under the influence of the open pit coal extraction activities carried out in the "El Cerrejón" open cast mine (La Guajira - Colombia). These strains were selected because of their ability to grow in a (AMSC5) growth medium with powdered LRC at 5% as the only source of carbon. Its composition (mg/L) was: NH₄NO₃ 2.50, KH₂PO₄ 1.75, MgSO₄ 0.75, K₂HPO₄ 0.75, NaCl 0.25, ZnSO₄ 0.088, FeCl₃ 0.08, CuSO₄ 0.016, MnCl₂ 0.014, MoO₃ 0.007, Co (NO₃)₂ 0.005; noble agar 15 g.L^-1, powdered LRC 5%(p/v) (Valero et al., 2011).

LRC Characterization and Extraction of HS Through the Classical Method: the LRC used in the study was extracted from mantle number 40 of the pit named "Tajo Patilla" of the "El Cerrejón" open cast mine (11°05'45.54" N and 72°40'66.55" W). The LRC was sieved to obtain particles smaller than 300 m. The content of heavy metals (As, Co, Pb, V, Cu, Zn, Ni, Cr, B, Mo and Cd) was determined together with total humidity, ash content, calorific power, content of volatile substances, percentage of fixed carbon, sulfur, and minerals in the ashes (Fe₂O₃, CaO, MnO₂, MgO, SrO, K₂O, BaO). This was done in compliance with the AMTS (American Society for Testing and Materials) standards. Additionally, a Fisions Interscience EA 1108 analyzer was used to determine elemental composition (C, H, O, N).

The HS of the LRC were obtained through the classical extraction method using 0.5 M of NaOH. The fractions of humic acids (HA) and fulvic acids (FA) were separated in accordance with the protocol described by Sharif et al. (2002). The percentage of carbon in the total humic extract (THE) and in the fractions of HA and FA was determined by using the methodology described by the International Humic Substances Society (2007).

LRC Solubilization Test in a Solid Matrix: Each strain was massively cultivated on nutrient agar plates (Oxoid). Cultures were incubated for 48 h at 32 °C. Afterwards, sterile LRC particles were placed on the culture's surface; their diameter ranged from 2.36 to 4.25 mm, and they were incubated for 8 days at 30 °C. LRC solubilization was detected by the presence of a brown halo indicating HS diffusion around the particle (Steinbuchel 2001).

LRC Solubilization Test in a Submerged Growth Medium: the bacterial cultures in AMSC5 were used to prepare an inoculum with a concentration level of 0.5 in the McFarland scale. This preparation was inoculated into flasks containing 100 mL of nutrient broth supplemented with 0.001% of HS acting as an inducer of coal solubilizing activity (Yuan et al., 2006). The cultures were incubated at 37 °C for 48 h. Later on, 1 g of powdered LRC that had been previously sterilized by autoclave was added to each tube. The resulting cultures were then incubated at 30 ± 2 °C in orbital shaking at 420 rpm. After 7 days, the pH was determined and each culture was centrifuged at 3200 rpm for 15 min. The brown supernatant was filtered on a Whatman paper whose pore diameter was 2.5 µm. Absorbance of the resulting filtrate was measured in a Genesis 20- 4001-4 spectrophotometer at 465 nm in order to estimate the amount of SH present in the medium (Yuan et al., 2006). The remaining LRC in each culture underwent three centrifugation (7000 rpm for 15 min) and water washing cycles. It was then dried at 100 °C until it reached constant weight. After this, the LRC was weighted to determine the percentage of LRC that had been transformed. The experiment was performed in triplicate.The growth medium with an addition of LRC and no inoculum was used as the control culture. The growth medium without LRC or inoculum was used as the target.

To determine the concentration of HS released from the LRC by bacterial activity into the growth medium, an absorbance curve was created using HS solutions with concentrations ranging from 0.1 and 1.6 mg.mL^-1. The equation of the curve made it possible to conduct a linear regression analysis using the absorbance values taken from the extracellular filtrates obtained. Results of percentages of CBR transformed, HS concentration in the medium and pH were subjected to a one-way analysis of variance, means of each variable were also compared trough Dunnet method with a significance level of 95%, the ANOVA analysis and mean comparison tests were performed using SPSS software version 18.

Molecular Typing of Efficient Strains: the DNA of the bacteria strains with the best performance in terms of HS production was extracted. A 1465 pb region of the 16s ribosomal gene was amplified via PCR using primers 27F, 1492R, 518F, and 800R. The products of the reaction were sequenced and assembled in a consensus sequence problem. This sequence was later compared with reference databases from the US National Center for Biotechnology Information (NCBI), thus generating the taxonomic classification by means of a phylogenetic tree of the group of 25 sequences that most closely resemble the consensus sequence.

Characterization of HA Through Elemental Analysis (C,H,O,N), Infrared Analysis (IR), and E₄/E₆ Ratio: the fraction of HA obtained from the LRC solubilization process using the bacterial strain with the best performance was compared with the fraction of HA obtained with NaOH 0.5 M. Elemental composition (C, H, N, O) was determined with a Fisions Interscience EA 1108 analyzer, and the result was corrected for the ash content in each sample, which was in turn determined through the combustion of 50 mg of each sample at 650 °C for 4 h. To obtain the IR spectrum, diffuse reflectance was recorded with the subsequent Fourier transform (DRIFT) in a PE Spectrum One spectrometer equipped with an accessory for diffuse reflectance. During this process, up to 100 scans per sample were accumulated at a resolution of 4 cm^-1. Before the DRIFT analysis, the dried samples were diluted by mixing them with KBr powder (5/100 Wt/Wt) in an agate mortar. To determine the E₄/E₆ ratio, 4 mg of HA was dissolved in 10 mL of NaHCO₃ 0.05 M, then pH was adjusted at 8.3 with NaOH 0.1 M, and finally, absorbance was measured at 465 and 665 nm in a GENESYS 10S UV-VIS spectrophotometer.

Results

LRC Characterization: the humidity of the LRC used in this study was 28.44%, 11.12% of the coal was ash, and 47.79% volatile substances. Similarly, the calorific power was 4781 Kcal.Kg^-1, 41.09% of the coal had fixed carbon, and 0.13% of its composition was S. These results confirm that this is a lignite-type LRC given its humidity and high content of volatile materials and the fact that its calorific power is below 6390 kcal/kg^-1. The elemental analysis showed that 46.04% of the LRC was C, 3.26% H, 42.95% O, and 1.38% N. The minerals in the ash were Fe₂O₃ 4.24%, CaO 69.3%, MnO₂ 0.14%, MgO 9.37%, SrO 0.89%, K₂O 0.05%, and BaO 0.08%. The process for determining the presence of As, Co, Pb, V, Cu, Zn, Ni, Cr, B, Mo, and Cd yielded the following values respectively: 0.71, 2.31, 1.73, 1.66, 0.55, 22.43, 3.35, 2.4, 15.11, 2.52, and 0.08 ppm. The process for extracting HS from LRC using NaOH 0.5 M reached a performance level of 44.68 ± 7.27%. The carbon content in the total humic extract (CTHE) was 32.91%; the carbon in humic acids (CHA) was 24.31%; and the carbon in fulvic acids (CFA) was 8.6%.

LRC Solubilization in a Solid Matrix: four out of the 19 strains evaluated (CSB34, CSB10, CSB3, and CSB13), developed a brown halo around the LRC particle (Figure 1a). Their average diameters were 40, 38, 15, and 12 mm respectively.

LRC Solubilization in a Submerged Growth Medium: all the bacterial cultures with LRC additions developed a brown color that is typically observed in HS (Yuan et al., 2006) (Figure 1b). Such color is associated with an increase in absorbance at 465 nm. The concentration of HS reached values between 127 and 3100 mg/L(Figure 2a). The absorbance value observed at 465 nm in the control treatment indicates that spontaneous release of small amounts of HS from the LRC took place upon contact with the growth medium. The Dunnet comparison average analysis made it possible to group activities of the CSB into five groups (Figure 2a). There was a significant difference (α = 0.05) between almost all the treatments and the control treatment. An exception to this was the isolated strains from group (a). Strains CSB3, CSB13, and CSB25, which make up group (d), were the most active, and their HS production ranged between 2000 and 3100 mg/L. The values for LRC weight loss due to bacterial activity varied from 25 to 37% (Figure 2b). In addition, a weight loss rate of 6.7% was observed in the control treatment.

The addition of LRC raised the pH of the growth medium to a value close to 5 (Figure 3). Nevertheless, this change was reverted for all the bacteria cultures and the pH reached values ranging from 7.1 to 8.4. Likewise, a correspondence was observed between the strains with higher HS production (e.g. strains CSB3, CSB10, and CSB25) and higher pH values (8-8.5).

Molecular Typing: Table 1 shows the results of typing strains CSB 25, CSB3, CSB13, and CSB10, which showed the highest values regarding HS production in a liquid growth medium. The high rate of similarity between the identifiers of the gene bank and the analyzed sequences for the 4 strains studied indicates that these strains are likely to be Bacillus mycoides, Microbacterium sp, Acinetobacter sp. and Enterobacter aerogenes respectively. Of these genera, only the Bacillus genus has been reported due to its capacity to solubilize coal (Pokorny et al., 2005). The strains of the other three genera are new reports on coal solubilizing bacteria.

Characterization of the HA: the values of the E₄/E₆ ratio were 5.2 for the HA obtained through B mycoides, and 4.8 for the HA obtained through the classical method.

The IR spectra of the HA obtained through LRC solubilization with the CSB 25 strain (Bacillus mycoides) (Figure 4a) and those of the HA extracted with the classical method (Figure 4b) showed similar qualitative characteristics regarding the presence of organic functional groups.

There were vibrations due to the stretching of O-H alcohols or phenols in polymeric association (3400-3200 cm^-1). Likewise there were bending vibrations in the O-H plane of alcohols and phenols around 1400 cm^-1. Additionally, C=N bond-stretching bands were observed between 2000 and 2600 cm^-1 in secondary amides. Absorption bands were observed between 1500 and 1600 cm^-1, which is associated with the C=C vibrations typically observed in aromatic hydrocarbons and carboxylic groups. Around 1650 cm^-1, a band was observed which corresponds to the vibration of the C=C bonds conjugated with C=O and COO^-; this band is related to the presence of unsaturated ketones, carboxyl groups or aryl esters as well as primary amides. Around 1100 cm^-1 in the specter of the HA obtained through bacterial activity, a band was observed which is typically present in aromatic rings with para- and ortho-substitutions. Between 890 and 700 cm^-1, bands were observed which are typically found when there is stretching in the C-O-C bonds of carbohydrates.

The elemental composition of the HA (See Table 2) showed a lower content of N, C, and H, and a higher content of O in the HA obtained through classical methods.

Discussion

The percentage of extraction yield of HA through the classical method, CEHT, CAH, and CAF, indicates that the LRC used is a considerable source of HS; therefore it may be a substrate prone to the activity of coal solubilizing bacteria. The solubilization of LRC in a solid medium with the development of a brown halo has been previously observed for most LRC solubilizing fungi (Steinbuchel 2001) and for the Streptomyces setonii and Streptomyces viridosporous bacteria (Strandberg and Lewis, 1987).

The brown color, the increase in absorbance to 465 nm and the LRC weight loss in the control treatment provide evidence of the spontaneous solubilization of the LRC in the growth medium. The strains CSB3, CSB13, CSB10, and CSB25 which caused a greater production of HS also caused the greatest decline in LRC in the culture medium; although some strains that exhibit high values of transformed LRC produced low amounts of HS (CSB5, CSB7, CSB14 ,CSB15, CSB17, CSB20, CSB22 and CSB23). This result suggests that these strains have the ability to transform LRC but they also absorb the solubilized substances or transform them into other products other than HS; therefore, we can infer that all the strains under study exhibit a considerable ability to use and exploit LRC, but only some strains make it possible for HS to remain in the growth medium; these strains can be considered as the most efficient in terms of net production of HS.

The pH reached in the culture medium, despite the acidification effect from the LRC suggests that the CSB expressed the production of alkaline substances as one of the mechanisms to solubilize LRC; this phenomenon has been described in previous studies (Hofrichter et al., 1997; Yuan et al., 2006). The alkaline substances may be generated in the medium as a result of the transformation of nitrogen-rich compounds; for example, alkaline amines are produced as a result of the metabolism of peptones present in the nutrient broth (Hofrichter et al., 1997).

The values of the optical densities ratio (E₄/E₆) for HA generally range between 3 and 8.5 (Stevenson 2004); the values ??found for the two types of HA in this study are considered to be similar and indicated an intermediate to high degree of humification; the result suggests that the supramolecular structure of the HA has a moderately high molecular weight, caused by molecules with a high aromatic condensation but with the presence of aliphatic chains, carboxylic groups, and an intermediate level of oxygen.

The IR analysis revealed no significant qualitative differences regarding the predominant organic groups in the macrostructure of the two HA types (Figure 3). However, the basic composition of the HA indicates that bacterial activity on the LRC generates N-, C-, and H-enriched HA, but with a lower oxygen content; this result evidences the activity of bacteria on the oxygen functional groups, which are the most reactive groups within the HS. This fact is possibly a direct consequence of the microbial metabolism that causes structural changes to the HA. The O/C atomic ratio is considered an indicator of carbohydrates and carboxylic groups, as well as the degree of humification (Canellas and Rocha, 2004); the decrease in this ratio suggests an increase in the HA aromatic condensation produced by B. mycoides, associated with the reduction of carbohydrates and carboxylic groups possibly used by bacteria. The value of the H/C ratio also shows the level of maturity in the HS, because it indirectly reflects the existence of more condensed aromatic structures or substitutions in cyclic structures (Lu et al., 2000).The result evidences that the HA obtained through B. mycoides have a higher aromatic condensation and a lower content of aliphatic groups. The C/N atomic radius reflects the enrichment of nitrogenous structures in the HA released from the LRC through bacterial activity. The above findings indicate some degree of structural change in the HS associated to its release from coal through bacterial activity.

The strains evaluated in this study were isolated from microhabitats which have been permanently enriched with residues from the extraction, washing and storage of coal (Valero et al., 2012).These strains evidence the biotransforming ability of LRC to produce SH in vitro. Strains with greater activity are regular soil inhabitants, this fact indicates that, probably under natural conditions, an adaptation of the microbial populations which use and transform coal took place; this fact is reflected in the structural differences found in the HA produced by B. mycoides.

Likewise, it has been observed that, in reconstructed soils from closed coal mines, part of the carbon stabilized on the humified organic matter is derived from coal waste (Dick et al., 2006). Additionally, LRC is humified at a rate of 0.25 g.kg of soil^-1.year^-1 after the establishment of the microbial community and after an increase of ligninolytic enzymes (Rumpel and Kogel, 2002). In addition, given the content of heavy metals in the LRC, it represents no risk of toxicity, as it does not surpass the maximum permissible limits for contamination with heavy metals if used in natural environments such as soil, in compliance with the Alloway (1995) regulations. On the contrary, LRC can be considered as a source of elements such as Cu, Zn, Mo, Co, and B, which are necessary for plant nutrition. Its elemental composition also provides nutritive elements such as C, N, S Mg, and K, which are essential for the development of microorganisms. This composition also provides micronutrients such as Fe, Ca, and Mn.

In spite of the technical and economic difficulties to carry out the biotransformation of LRC in large scale bioreactors, the findings presented in this paper make it possible to suggest that in situ LRC solubilization using the soil microorganisms involved in complex transformation processes of organic matter can trigger the release of humified organic matter. Thus, this phenomenon may be helpful in soil reclamation processes.

Acknowledgments

The authors would like to thank the company Carbones del Cerrejón Limited, as well as COLCIENCIAS for sponsoring this research. They also thank the universities Universidad Popular del Cesar, Universidad Nacional de Colombia, and the Research group on Supramolecular Humic Systems in the Environment at Universitat di Napoli Federico II.

Submitted: June 16, 2013

Approved: March 14, 2014

All the content of the journal, except where otherwise noted, is licensed under a Creative Commons License CC BY-NC.

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Publication Dates

• Publication in this collection
  04 Nov 2014
• Date of issue
  Sept 2014

History

• Accepted
  14 Mar 2014
• Received
  16 June 2013