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BMC Biotechnology

Research article
Open Access

Optimal reduction of chemical oxygen demand and NH3–N from landfill leachate using a strongly resistant novel Bacillus salmalaya strain

  • Arezoo Dadrasnia1, 2,
  • Mohd Sofian Azirun1 and
  • Salmah Binti Ismail1Email author
BMC Biotechnology201717:85

https://doi.org/10.1186/s12896-017-0395-9

©  The Author(s). 2017

Received: 10 April 2017

Accepted: 31 October 2017

Published: 28 November 2017

Abstract

Background

When the unavoidable waste generation is considered as damaging to our environment, it becomes crucial to develop a sustainable technology to remediate the pollutant source towards an environmental protection and safety. The development of a bioengineering technology for highly efficient pollutant removal is this regard. Given the high ammonia nitrogen content and chemical oxygen demand of landfill leachate, Bacillus salmalaya strain 139SI, a novel resident strain microbe that can survive in high ammonia nitrogen concentrations, was investigated for the bioremoval of ammonia nitrogen from landfill leachate. The treatability of landfill leachate was evaluated under different treatment parameters, such as temperature, inoculum dosage, and pH.

Results

Results demonstrated that bioaugmentation with the novel strain can potentially improve the biodegradability of landfill leachate. B. salmalaya strain 139SI showed high potential to enhance biological treatment given its maximum NH3–N and COD removal efficiencies. The response surface plot pattern indicated that within 11 days and under optimum conditions (10% v/v inoculant, pH 6, and 35 °C), B. salmalaya strain139SI removed 78% of ammonia nitrogen. At the end of the study, biological and chemical oxygen demands remarkably decreased by 88% and 91.4%, respectively. Scanning electron microscopy images revealed that ammonia ions covered the cell surface of B. salmalaya strain139SI.

Conclusions

Therefore, novel resistant Bacillus salmalaya strain139SI significantly reduces the chemical oxygen demand and NH3–N content of landfill leachate.

Graphical abstract

Leachate treatment by B. salmalaya strain 139SI within 11 days.

Keywords

Ammonia nitrogen Bacillus salmalaya BioremovalBioengineering processLandfill leachate

Background

Over the past few years, the generation of municipal solid wastes in Malaysia has considerably increased due to rapid urbanization, capital development, and improving socioeconomic levels [1]. The amount of waste generated in Kuala Lumpur has rapidly increased from 587 tons/day in 1990 to 3701 tons/day in 2012 (0.9 kg/capita/day) [2]. In Malaysia, approximately 95% of collected wastes are dumped into 261 landfills given the inexpensive operating costs, easy set-up, and low supervision requirement of landfill sites [2, 3]. Consequently, the generation of landfill leachate is a major issue associated with the disposal of municipal solid waste. Inadequate treatment strategies for landfill leachate have recently become a considerable concern given that that the rate of waste generation is outpacing the rate of human population growth; furthermore, highly toxic hazardous waste is directly disposed into rivers or may percolate through soils and pollute receiving waters [3]. Various techniques have been proposed to address this environmental problem; among these techniques, bioaugmentation is an environmentally friendly and the most effective method to resolve the issue of landfill leachate [4, 5]. A serious issue of landfill leachate is its high content of ammonia nitrogen (NH3–N), which prevents the activity and growth of microorganisms due to accelerate eutrophication and an increased dissolved oxygen reduction as well as toxic effects on aquatic organisms. Conventional treatment methods are challenging, especially for mature or old landfill leachate with NH3–N levels [6–8]. Organic matter in leachate is quantified by biochemical oxygen demand (BOD) and chemical oxygen demand (COD).

Given their economy and feasibility, biological techniques are important methods for treating landfill leachate. Oxidation, electrocoagulation, microfiltration, and photo catalysis are commonly used to remove high COD and NH3–N from landfill leachate. All of these processes, however, are costly and can cause secondary pollution in some cases. Therefore, a relatively new treatment technique should be developed. Many techniques, such as nanofiltration [9], reverse osmosis [10], membrane bioreactor [11], up flow anaerobic sludge blanket combined with aerobic reactor [12], and adsorption by activated carbon [13], have been used to remove NH3–N and COD. Deng and Englehardt [14] treated leachate with hydrogen peroxide-improved iron and aeration; they found that the BOD/COD ratio increased from 0.02 to 0.17 and that NH3–N removal increased by 83%. These authors also reported that the electrochemical oxidation of landfill leachate under appropriate conditions removes most NH3–N and COD. However, the two main drawbacks of electro-oxidation are high energy consumption (more expensive operating costs than those of biological processes) and the potential formation of chlorinated organic compounds. Introducing microorganisms with high biodegradation ability and resistance to NH3–N, BOD, COD, and humic acid might be a promising solution to the problems associated with the treatment of landfill leachate. The presence of microbes in air, soil, and water environments enhances transformation and degradation during remediation [15]. Hence, microbes are important in the degradation of complex compounds. Bioaugmentation is a highly efficient and straightforward technology for removing pollutants from contaminated environments; this method could improve long-established treatment operations and decrease energy utilization [16, 17]. The main factor that affects the success of bioaugmentation is the ability of the added bacteria to adapt to and efficiently degrade pollutants under natural conditions [18, 19]. Highly adaptive bacteria stimulate the highly efficient removal of pollutant substances. To our knowledge, there are few studies on the removal of NH3–N from landfill leachate via bioaugmentation. The present study aimed to evaluate the efficiency of a novel bacteria (Bacillus salmalaya strain 139SI) that was isolated from agricultural soil in Malaysia; previous studies have shown that this bacterial strain has the ability and potential to degrade polycyclic aromatic hydrocarbons and sorb heavy metal [20, 21] and consequently decrease the high toxicity values of BOD, NH3–N, and COD in landfill leachate under different environmental circumstances.

Methods

Isolation and identification of strain

B. salmalaya was originally isolated from indigenous agricultural soil in Malaysia (2.99917°N, 101.70778°E). New strains were isolated with Brain–Heart–Infusion (BHI) agar as a highly nutritious growth medium which contains sodium chloride 5 g, disodium phosphate 2.5 g, dextrose 2 g, brain heart (infusion solids form) 8 g, agar 13.5 g, pancreatic digest of animal tissue 5 g, pancreatic digest of Casein 16 g, and supplemented with 5% sheep blood in 1 l. Among the isolated strains, 139SI exhibited strong hemolytic activity. On the basis of 16S rRNA sequencing and phylogenetic analysis, this strain was designated as a novel strain. Further information and molecular analysis of strain 139SI were reported recently [18, 19].

Leachate sample

Leachate samples were obtained from an untreated leachate pond at the Bukit Beruntung landfill in Malaysia (3°25′32.14″N, 101°32′56.6″E); this landfill is a non-sanitary, open dumping and an operational landfill. Bukit Beruntung landfill (operated in 1992), which is visible from the North-South Highway, receives approximately 80 t of waste daily. The depression in the hilly area allows the expansion of the disposal site. Lack of enforcement by local municipality resulted in illegal dumping of municipal solid waste along the road to the landfill site.

Determination of the minimum inhibitory concentration of NH3–N

To determine whether B. salmalaya strain 139SI is resistant to ammonia nitrogen, the following test was performed. First, strain pellets were prepared by centrifuging culture broth (OD600 = 1.0) at 3500 rpm for 15 min. These pellets were added into 10 mL of leachate with 1000 ppm concentration of NH3-N and incubated at 35 °C and 150 rpm for 72 h. Subsequently, bacteria were harvested and resuspended in leachate, which contained 2000 ppm ammonia nitrogen. The bacterial/leachate mixture was incubated under the above conditions. This process was repeated at different concentration and it was completed when the final concentration of NH3-N in the landfill leachate was 100 g/l. Approximately 20 μL of the each above mixture was spread onto a plate of solid medium and incubated at 35 °C for 16 h. The culture medium comprised BHI and leachate in 2:3 ratio and was solidified with agar. Pure colonies were selected, cultured, and stored for further experimental work.

Bioaugmentation process

Pure B. salmalaya strain 139SI colony was cultured in BHI culture medium for 24 h at 33 °C and 150 rpm. Afterward, the biodegradation experiment was performed with 30 mL of landfill leachate inoculated with 3 mL bacterial strain (OD600 = 1) and incubated at 30 °C for 11 days at 150 rpm. Samples were collected and analyzed at 1, 3, 5, 8, and 11 days. To test the biodegradation capability of B. salmalaya strain 139SI and to remove the effect of indigenous bacteria, sterilized landfill leachate was degraded under same conditions.

Effects of environmental conditions on bioaugmentation

To determine the effect of various conditions on the degradation efficiency of B. salmalaya strain 139SI, experiments were carried out at different temperatures (30 °C, 35 °C, and 40 °C), pH values (6, 7, and 8), and inoculum dosage (1, 3, and 5 mL). Experiments were performed in triplicate. Design-Expert Software was used to analyze experimental data. Significant effect on biodegradation was determined at 95% level (P < 0.05) using SPSS version 18.

Elemental analysis

The decreases in the values of NH3–N, COD, and BOD were measured to evaluate the effectiveness of the microbial treatment of landfill leachate. COD concentration was determined on the basis of the agreed methods for Water and Wastewater examination (APHA 5220C). Samples were diluted and added to standard COD ampules and incubated in a dry incubator at 150 °C for 2 h. The COD tubes were allowed to cool down to room temperature and titrated with 0.05 M ferrous ammonium sulfate. NH3–N concentration was measured by APHA 4500 NH3 F-Phenate method. The sample was transferred to a 50-mL conical flask and mixed with the following solutions: phenol (1 mL), sodium nitroprusside (1 mL), and oxidizing solution (2.5 mL). The sample was covered and allowed to settle for at least 1 h and to develop color at room temperature (22–27 °C) in subdued light. Subsequently, the absorbance was read at 640 nm using spectroquant PHARO 100 [4]. BOD concentration was measured using APHA 5210 B method. Removal percentage was computed on the basis of the concentration measurement using the following equations:
$$ {\mathrm{Removal}}_{\mathrm{COD}}\left(\%\right)=\left[\left({\mathrm{COD}}_{\mathrm{i}}\hbox{--} {\mathrm{COD}}_{\mathrm{f}}\right)/{\mathrm{COD}}_{\mathrm{i}}\right]\times 100\%, $$
(1)
$$ {\mathrm{Removal}}_{\mathrm{N}\mathrm{H}3\hbox{--} \mathrm{N}}\left(\%\right)=\left[\left({\mathrm{N}\mathrm{H}}_3-{\mathrm{N}}_{\mathrm{i}}\hbox{--} {\mathrm{N}\mathrm{H}}_3-{\mathrm{N}}_{\mathrm{f}}\right)/{\mathrm{N}\mathrm{H}}_3-{\mathrm{N}}_{\mathrm{i}}\right]\times 100\%. $$
(2)
where i and f are the initial and final concentrations, respectively.

The morphology of cell surfaces (before and after adsorption) was evaluated with scanning electron microscopy (SEM, SEI quanta SEG 450, Netherlands).

Results

Raw leachate characteristics

The pH value of raw leachate was 8.3 ± 0.2. According to previous reports, the pH of old leachate is higher than 7.5; furthermore, the pH of stabilized leachate shows little variations and is in a fairly constant range of 7.5–9.0. The pH value of young leachate, however, is less than 6.5 [7, 22].

Minimum inhibitory concentration of NH3–N

NH3-N tolerance test for the 139SI strain was performed in order to investigate the endurance ability of Bacillus salmalaya to growth at different concentration of NH3-N (from 1 to 100 g/l). However, none of the members of Bacillus salmalaya and has been reported to possess simultaneous COD and NH3-N removal abilities and such high NH3-N tolerance ability. Therefore, it was necessary to investigate the augmented performances of this novel bacteria to treat high NH3-N containing landfill leachate.

Evaluation reduction of COD and NH3–N

The successful bioaugmentation and removal of leachate depend on the ability of the introduced bacteria to perform its activities and survive in different environmental conditions. Figure 1 shows COD removal rate in unsterilized and sterilized landfill leachate during the 11 days of study. Statistical analysis showed a significant difference between leachates that were amended with culture or with the control treatment. The highest COD removal rate was observed in leachates that were amended with bacteria. The obtained results confirmed the ability of B. salmalaya strain 139SI to decrease COD under unsterilized conditions with a high rate of 81% after 5 days; this rate became constant in the following days and continued to increase and reached approximately 91.4% on day 11 (Fig. 1). The same trend was observed in sterilized amended samples, which showed a maximum COD reduction of 55.7% on day 11 (data showed no further increase in COD removal with the extension of degradation time). Sterilized landfill leachate without bacterial amendment was used as the control. The control showed 39% removal rate, which was lower than that of the inoculum. This result proved the significant effect of strain on degradation. NH3–N removal under both sterilized and nonsterilized conditions showed trends that were similar to those of COD removal, as shown in Fig. 2. The highest percentage of NH3–N reduction under unsterilized conditions was 78% in treatments that were amended with strain 139SI on day 11; this percentage was higher than that of the indigenous bacteria (28.1%).
Fig. 1

Amount of COD removed from unsterilized and sterilized landfill leachate by Bacillus salmalaya strain 139SI at different hydraulic retention times. Vertical bars indicate SE (n = 3)

Fig. 2

Percentage of NH3–N removed from unsterilized and sterilized landfill leachate by B. salmalaya strain 139SI at different hydraulic retention times. Vertical bars indicate SE (n = 3)

Correlations between BOD and COD

The high correlation (r2 = 0.92) between BOD and COD indicated the presence of organic matter in non-sterilized leachate landfill (Fig. 3a); organic matter can be readily degraded by the application of microorganisms. The organic matter in leachate was characterized on the basis of the different levels of biodegradability, which was defined with the mass concentration ratio of BOD: COD. This ratio indicates the degrees of both chemical and biological decompositions of pollutant leaching from landfills. The low BOD/COD ratio indicated the increased concentration of non-biodegradable organic compounds and consequently the difficulty of biodegradation [23, 24]. In the present study, this ratio continued to slowly and steadily increase from 0.26 to 0.36 with the increase of time treatment after microbial amendment. Biomass growth kinetics for non-sterilized sample amended with strain 139SI was observed during the 11 days of study (Fig. 3b). The high amount of biomass demonstrated that the B. salmalaya strain can tolerate the high COD and NH3–N concentrations and can enhance landfill leachate treatment.
Fig. 3

a Correlation between biochemical oxygen demand and COD. b Microbial growth kinetics. (Non-sterilized leachate sample) Vertical bars indicate SE (n = 3)

Response surface plots

The effect of temperature (I), pH (II), and inoculum size (III) at three levels were investigated to optimize the removal of COD, BOD, and NH3–N by B. salmalaya strain 139SI. 3D response surfaces were drawn using Design-Expert Software 10. As shown in Fig. 4a, b, and c, the highest reduction in NH3–N (151 mg/L) occurred at pH 6 (II1), temperature of 35 °C (I2), and inoculum size of 3 mL (III2), which were identified as optimal conditions. According to statistical analysis (F values), the differential performance of variable parameters followed the order II > I > III. pH, temperature, and inoculum size exerted the largest effect on the removal rate of ammonia nitrogen (P value lower than 0.05).
Fig. 4

Influence of inoculum size, pH, and temperature on NH3–N, BOD, and COD removal

SEM analysis

Surface characterization via SEM is a useful, simple qualitative method to demonstrate the microbe morphology in leachate [25]. The surface morphology of the cells was analyzed via SEM before (Fig. 5a) and after (Fig. 5b) use in bioaugmentation. Bacterial cells were thin and rod-shaped prior to the treatment and changed in morphology after use in biodegradation (Fig. 5b). This event would describe the mechanism of adsorption that is attributed to the coverage of the cell surface, which appeared large and spongy, with ammonia ions. EDX as a useful tool for evaluating the elemental and chemical analyses of biosorbents was illustrated in the Fig. 5c. The percentage of nitrogen ions were presented as final peaks and demonstrated that the ions were attached to the cell surface. The EDX only infer the N atom, the reason for such readout in EDX might be contributed to the present of protein on the cell surface, or cell lysate deposit.
Fig. 5

Scanning electron microscope micrographs a before, b after bioaugmentation, and c EDX after the bioaugmentation process

Discussion

In this study, BOD and COD amounts were 1189 ± 62.8 and 4517 ± 82.8 mg/L, respectively. These obtained values exceeded the authorized or permissible values issued by the Malaysian Environmental Quality Acts 127 and 1974 [26]. This result clearly showed that leachate required treatment to be environmentally acceptable. The BOD5/COD ratio is an indicator of the changes in the amount of biodegradable compounds in landfill leachate [27]. A BOD5/COD ratio of 0.26 indicates that the leachate is stable and poorly biodegradable [22, 28]. In this study, NH3–N concentration in the leachate was 685 ± 14.7 mg/L. The increasing amount of NH3–N with increasing landfill age likely results from the fermentation and hydrolysis of the nitrogenous fragments of biodegradable refuse [25, 29]. The results of the tolerance test proved the ability of B. salmalaya strain 139SI to survive under high NH3–N concentration as high as 70 g/l, as evidenced by the high cell counts after 16 h of culture. This result confirmed that our strain possessed high endurance under specific environmental pressures. The maximum COD reduction of non-sterilized leachate without culture addition was approximately 41.4%, which showed that the inoculum is a key factor in enhancing biodegradation. The higher removal rate in the treatment samples that were amended with strain 139SI than that in the control could be attributed to the effect of enzyme production, biomass activity, and growth efficiency of the microorganism.

The results showed that B. salmalaya strain 139SI had higher removal efficiency for COD than for NH3–N. Sterilized degradation was investigated to eliminate the effect of autochthonous bacteria and to assess the ability of 139SI in the bioaugmented treatment of landfill leachate. During the whole experiment, the COD reduction continued to increase in control treatments; the rate of increase, however, was not significantly evident compared with that of amendment treatments. Bioaugmentation displayed higher effectiveness in COD removal among all amended treatments. Removal efficiency of NH3–N remarkably increased after the third day (47%) and improved until the last day of study. In a similar study, [6] reported that under optimum conditions (30 °C, pH 7.33, 4.14 days, and 170 rpm), 94.7% of NH4 +–N was removed from landfill leachates that were treated with 3.5 mL of inoculated domesticated bacteria. The same trend was obtained for the sterilized samples (Fig. 2). Amending the sterilized leachate with bacterial culture increased removal rates by 40% compared with the sterilized control without the strain. This result showed that almost all bacteria were killed due to sterilization (in this case, only 15% NH3–N could be removed). These results also showed that the degradation ability of B. salmalaya strain 139SI was in the order of COD and NH3–N. In our future study, we will propose a simple field trial to explore the potential of strain 139SI in landfill leachate treatment.

The highest reduction on COD (385 mg/L) and BOD (141 mg/L) was recorded at pH 7 (II2), inoculum size 3 mL (III2), and 30 °C (I1). These results indicated significant interactions between each factor during bioaugmentation. A recent research conducted by [25] on the Pulau Burung Landfill Site in Malaysia indicated that the optimum variable conditions for COD and NH3–N removal rates of 65.5% and 60.2%, respectively, under anaerobic condition were achieved with 100 mL of organism at pH 7 in a period of two weeks.

Conclusions

Results demonstrated that bioaugmentation with the novel strain can potentially improve the biodegradability of landfill leachate. B. salmalaya strain 139SI showed high potential to enhance biological treatment given its maximum NH3–N and COD removal efficiencies. The maximum NH3–N removal of >65% and >75% was achieved after 5 and 11 days, respectively. COD (91.4%) and BOD (88%) considerably decreased after the study period. Therefore, this bacterial strain has potential low-cost applications in the treatment of wastewater with high COD, BOD, and NH3–N contents. Results verified that applying a single strain to landfill leachate, which contains many kinds of pollutants, is a fast and efficient method to remove high levels of NH3–N and COD. This study provides useful information for the design and management of landfill leachate for the realistic prediction of future trends.

Abbreviations

BHI: 

Brain–Heart–Infusion

BOD: 

Biochemical oxygen demand

COD: 

Chemical oxygen demand

NH3–N: 

Ammonia nitrogen

OD: 

Optical density

SEM: 

Scanning electron microscopy

Declarations

Acknowledgements

The authors gratefully acknowledge Department of Biology, University of Malaya for the facilities and infrastructure. The authors also acknowledged the help rendered by KG Support Limited English editing service in proofreading the manuscript.

Funding

This work was financially supported by the University of Malaya Research Program grant number RP023B-14AFR in the design of the study, sample analysis, and providing instruments and grant number RP023A-14AFR in collection, analysis, and interpretation of data and in writing the manuscript.

Availability of data and materials

The datasets used and/or analysed during the current study are available from the corresponding author on reasonable request.

Authors’ contributions

AD designed the study plan, collected data, conducted the analysis and wrote the manuscript. MSA and SI provided critical reviews and comments of the manuscript, contributed to interpretation of the results and extensive text editing. All authors read and approved the final manuscript.

Ethics approval and consent to participate

The authors obtained the ethical approval for the soil collection from the owner of private farm (Mr. Shaul Hameed Bin Sellen) at No. 5, JalanBesarMerbau, Kg Bukit Hijau, Jeram, Kuala Selangor, Malaysia.

Consent for publication

Not applicable.

Competing interests

The authors declare that they have no competing interests.

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Authors’ Affiliations

(1)
Institute of Biological Sciences, Faculty of Science, University of Malaya, Kuala Lumpur, Malaysia
(2)
Institute of Research Management & Monitoring, University of Malaya, Kuala Lumpur, Malaysia

References

  1. Anwar J, Habib A, Haslenda H, Saeed I, Ahmed RM. Municipal solid waste management and potential revenue from recycling in Malaysia. Modern Appl Sci. 2014;8:1–13.View ArticleGoogle Scholar
  2. Iwan B, Chamhuri S, Basri H. Current status of municipal solid waste generation in Malaysia. J Adv Sci Eng Info Technol. 2012;2:16–21.Google Scholar
  3. Kamaruddin MA, Yusoff MS, Aziz HA, Hung Y-T. Sustainable treatment of landfill leachate. Appl Water Sci. 2015;5:113–26.View ArticleGoogle Scholar
  4. Renou S, Givaudan JG, Poulain S, Dirassouyan F, Moulin P. Landfill leachate treatment: review and opportunity. J Hazard Mater. 2008;150:468–93.View ArticleGoogle Scholar
  5. Wiszniowski J, Robert D, Surmacz-Gorska J, Miksch K, Weber JV. Landfill leachate treatment methods: a review. Environ Chem Lett. 2006;4:51–61.View ArticleGoogle Scholar
  6. Yu D, Yang J, Fang X, Ren H. Simultaneous efficient removal of high-strength ammonia nitrogen and chemical oxygen demand from landfill leachate by using an extremely high ammonia nitrogen–resistant strain. Biotechnol Appl Biochem. 2015;62:357–68.View ArticleGoogle Scholar
  7. Kurniawan TA, Lo W, Chan G, Sillanpaa MET. Biological processes for treatment of landfill leachate. J Environ Monit. 2010;12:2032–47.View ArticleGoogle Scholar
  8. Zulfikar MA, Novita E, Hertadi R, Djajanti SD. Removal of humic acid from peat water using untreated powdered eggshell as a low cost adsorbent. J Environ Sci Technol. 2013;10:1357–66.View ArticleGoogle Scholar
  9. Agenson KO, Urase T. Change in membrane performance due to organic fouling in nanofiltration (NF)/reverse osmosis (RO) applications. Sep Purif Technol. 2007;55:147–56.View ArticleGoogle Scholar
  10. Renou S, Poulain S, Givaudan JG, Moulin P. Treatment process adapted to stabilized leachates: lime precipitation–prefiltration–reverse osmosis. J Membrane Sci. 2008;313:9–22.View ArticleGoogle Scholar
  11. Bohdziewicz J, Neczaj E, Kwarciak A. Landfill leachate treatment by means of anaerobic membrane bioreactor. Desalination. 2008;221:559–65.View ArticleGoogle Scholar
  12. Liu M, Yang Q, Peng Y, Liu T, Xiao H, Wang S. Treatment performance and N2O emission in the UASB-A/O shortcut biological nitrogen removal system for landfill leachate at different salinity. J Ind Eng Chem. 2015;32:63–71.View ArticleGoogle Scholar
  13. Aziz HA, Adlan MN, Zahari MSM, Alias S. Removal of ammoniacal nitrogen (N-NH3) from municipal solid waste leachate by using activated carbon and limestone. Waste Manag Res. 2004;22:371–5.View ArticleGoogle Scholar
  14. Deng Y, Englehardt JD. Hydrogen peroxide-enhanced iron-mediated aeration for the treatment of mature landfill leachate. J Hazard Mater. 2008;153:293–9.View ArticleGoogle Scholar
  15. Dixit R, Wasiullah, Malaviya D, Pandiyan K, Singh U, Sahu A, Shukla R, Singh B, Rai J, Sharma P, et al. Bioremediation of heavy metals from soil and aquatic environment: an overview of principles and criteria of fundamental processes. Sustainability. 2015;7:2189.View ArticleGoogle Scholar
  16. Jiao Y, Zhao Q, Jin W, Hao X, You S. Bioaugmentation of a biological contact oxidation ditch with indigenous nitrifying bacteria for in situ remediation of nitrogen-rich stream water. Bioresource Technol. 2011;102:990–5.View ArticleGoogle Scholar
  17. Shao T, Yang G, Wang M, Lu Z, Min H, Zhao L. Reduction of oxidative stress by bioaugmented strain pseudomonas sp. HF-1 and selection of potential biomarkers in sequencing batch reactor treating tobacco wastewater. Ecotoxicology. 2010;19:1117–23.View ArticleGoogle Scholar
  18. Dadrasnia A, Usman MM, Wei KSC, Velappan RD, Jamali H, Mohebali N, Ismail S. Native soil bacterial isolate in Malaysia exhibit promising supplements on degrading organic pollutants. Proc Saf Environ Prot. 2016;100:264–71.View ArticleGoogle Scholar
  19. Ismail S, Dadrasnia A. Biotechnological potential of Bacillus salmalaya 139SI: a novel strain for remediating water polluted with crude oil waste. PLoS One. 2015;10(4):e0r120931.View ArticleGoogle Scholar
  20. Dadrasnia A, Ismail S. Biosurfactant production by Bacillus salmalaya for lubricating oil Solubilization and biodegradation. J Environ Res Public Health. 2015;12:9848.View ArticleGoogle Scholar
  21. Dadrasnia A, Chuan Wei K, Shahsavari N, Azirun M, Ismail S. Biosorption potential of Bacillus salmalaya strain 139SI for removal of Cr(VI) from aqueous solution. J Environ Res Public Health. 2015;12:1:15321–38.View ArticleGoogle Scholar
  22. Li W, Zhou Q, Hua T. Removal of organic matter from landfill Leachate by advanced oxidation processes: a review. J Chem Eng. 2010;2010:10.Google Scholar
  23. Zainol NA, Aziz HA, Yusoff MS. Characterization of Leachate from Kuala Sepetang and Kulim landfills: a comparative study. Energy Environ Res. 2012;2:4–52.View ArticleGoogle Scholar
  24. Ntampou X, Zouboulis AI, Samaras P. Appropriate combination of physicochemical methods (coagulation/flocculation and ozonation) for the efficient treatment of landfill leachates. Chemosphere. 2006;62:722–30.View ArticleGoogle Scholar
  25. Huliselan EK, Bijaksana S, Srigutomo W, Kardena E. Scanning electron microscopy and magnetic characterization of iron oxides in solid waste landfill leachate. J Hazard Mater. 2010;179:701–8.View ArticleGoogle Scholar
  26. MDC SB: Laws of Malaysia-Environmental Quality Act 1974 and Regulation. 4th ed Kuala Lumpur, Malaysia. Ministry of Natural Resources and Environment, Malaysia; 1997.Google Scholar
  27. Warith M. Bioreactor landfills: experimental and field results. Waste Manag. 2002;22:7–17.View ArticleGoogle Scholar
  28. Kamaruddin MA, Yusoff MS, Aziz HA, Basri NK. Removal of COD, ammoniacal nitrogen and colour from stabilized landfill leachate by anaerobic organism. Appl Water Sci. 2013;3:359–66.View ArticleGoogle Scholar
  29. Umar M, Aziz HA, Yusoff MS. Variability of parameters involved in leachate pollution index and determination of lpi from four landfills in Malaysia. J Chem Eng. 2010;2010. doi:10.1155/2010/747953.

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