Linking N2O emission from biochar-amended composting process to the abundance of denitrify (nirK and nosZ) bacteria community
© The Author(s). 2016
Received: 23 March 2016
Accepted: 11 May 2016
Published: 20 May 2016
Manure composting has been recognized as an important anthropogenic source of nitrous oxide (N2O) contributing to global warming. However, biochar effect on N2O emissions from manure composting is rarely evaluated, especially by linking it to abundance of denitrifying bacteria community. Results of this study indicated that biochar amendment significantly reduced N2O emissions from manure composting, primarily due to suppression of the nirK gene abundance of denitrifying bacteria. Pearson’s correlation analysis showed a significant positive correlation between nirK abundance and N2O fluxes, while a negative correlation between nosZ density and N2O fluxes. Simultaneously, a linear correlation between nirK gene abundance minus nosZ gene abundance with N2O fluxes was also observed. In addition, a statistical model for estimating N2O emissions based on the bacterial denitrifying functional genes was developed and verified to adequately fit the observed emissions. Our results highlighted that biochar amendment would be an alternative strategy for mitigating N2O emissions during manure composting, and the information of related functional bacterial communities could be helpful for understanding the mechanism of N2O emissions.
Nitrous oxide (N2O) is an important long-lived potent greenhouse gas contributing to current climate change, with 265 times greater global warming potential than that of carbon dioxide (CO2) on a mass basis over the 100-year time horizon (IPCC 2013). Manure composting as an important management strategy for sustainable use of livestock could reduce treatment costs but generate organic fertilizer for improvement of soil fertility (Larney and Hao 2007). However, manure composting leads to a large amount of nitrogen loss released as N2O or NH3 (Maeda et al. 2011). The annual global N2O emissions derived from manure composting were estimated to be 1.2 × 106 metric tons (Czepiel et al. 1996), which accounts for approximately 30–50 % of the annual global total of agricultural N2O emissions in most countries (Chadwick et al. 2011). Therefore, it is of great concern on developing effective alternatives for reducing N2O emissions and nitrogen losses during manure composting.
Recently, the importance of microbial traits involved in N2O production processes has gained worldwide concern (e.g., Maeda et al. 2011). It has been reported that N2O emissions from manure composting mainly occurred at the cooling stages of composting during denitrification driven by bacteria (Maeda et al. 2011), i.e., NO3 −, NO2 −, NO, and N2O are sequentially reduced by the catalyzation of nitrate reductase (narG), nitrite reductase encoding (nirS/nirK), nitric oxide reductase (norB), and nitrous oxide reductase (nosZ, functional for yielding N2), respectively (Maeda et al. 2011; Wang et al. 2013). Therefore, N2O emissions during manure composting are the result of net balance between its production (NO3 − → N2O) and consumption (N2O → N2) (Maeda et al. 2011). Several previous studies have investigated the dynamics of these functional genes abundance involved during manure composting processes under different conditions, and highlighted their interplay with observed N2O emissions and physicochemical characteristics (Angnes et al. 2013; Wang et al. 2013). Unfortunately, although the microbial pathways involved in N2O formation have been well documented, most of the established statistical models for estimating N2O emissions were currently still limited based on physicochemical parameters but without taking the microbial traits into consideration (Hu et al. 2015).
To date, various options have been reported for mitigating N2O emissions from manure composting, including the composting parameters modulation (e.g., C/N ratio, water content, pH), N2-fixing bacteria inoculation, and material amendments (Dias et al. 2010; Ogunwande et al. 2008; Pepe et al. 2013; Wang et al. 2013). Recently, biochar amendment has been increasingly encouraged as a potential approach for reducing N2O emissions from both manure composting systems and soils (Kammann et al. 2012; Wang et al. 2013). As a carbon-rich material derived by slow pyrolysis of biomass, biochar amendment can help to improve the NH3/NH4 + retention during the composting process (Steiner et al. 2010). Wang et al. (2013) examined the dynamics of functional microbial community during the windrow composting process, and revealed a correlation between the denitrifying bacteria and N2O emissions, but lack of a systematic link using the modeling approach.
In this study, an in situ measurement of N2O fluxes as regulated by biochar amendment over the whole life-cycle of manure windrow composting was taken to address the following concerns: (1) to evaluate the role of biochar in regulating N2O emissions during the composting process; (2) to give an insight into the interplay between N2O emissions and the abundance of relevant functional genes involved in denitrification; (3) and to develop a statistical model for estimating N2O emissions by integrating both the bacterial functional genes and physiochemical parameters. The results of this study would help to advance our knowledge on the potential effects of biochar for mitigating N2O emissions during manure composting, and simultaneously establish a link between N2O fluxes and the information of related functional bacterial communities.
Materials and methods
The windrow composting experiment was initiated on December 24, 2013 in a commercial organic fertilizer company (Jiangyin Lianye Biological Science and Technology Co., Ltd), located in Jiangsu Province, China. The total composting period was lasted for 64 days, and two types of composts were carried out: CK and Biochar. Each treatment was set up with three replicated composting piles. Each plie was sized as 12 m (length) × 2.8 m (width) × 1 m (height). Before the piles were constructed, compost feedstocks, including cattle manure and rice-chaff, were mixed in a ratio of 75:25 % (v/v) on a fresh weight basis. The cattle manure and rice straw were obtained from a cattle ranch and local paddy rice fields, respectively. The piles of biochar were received an additional biochar amendment with 3 % (w/v). Biochar used in this study was produced from wheat straw at a temperature of approximately 450 °C from a local company. Physicochemical properties of biochar were listed as follows: a total C content of 467.0 g kg−1, a total N content of 5.6 g kg−1, a pH of 9.4 (1:2.5 H2O), cation exchange capacity of 24.1 cmol kg−1 and ash content of 20.8 %.
The composting process can be generally divided into two phases. The phase I was the bio-oxidative phase that mechanical turning was taken once every 2 days for 24 days (December 24, 2013 to January 16, 2014). Thereafter, the piles were moved to the aside place for post-maturation during the phase II. The phase II was the cooling and maturing phase without pile turning for 40 days (January 17, 2014 to February 26, 2014) (Bernal et al. 2009; Chen et al. 2014).
Measurement of N2O fluxes
Besides that gas samples were collected regularly once a week over the whole composting process, supplementary gas sampling episodes were occasionally taken as needed to capture high flux peaks for the two pile treatments. The N2O emission was simultaneously measured using a modified vented chamber method (Chen et al. 2014; Hou et al. 2001; Mosier and Hutchinson 1981; Zou et al. 2005). Before sampling, PVC chamber bases (30 cm length × 30 cm width × 25 cm height) were pre-inserted 25 cm into the peak of piles to reduce the disturbance. When gas sampling, the opaque chamber (30 cm length × 30 cm width × 50 cm height) was placed on the bases and the bottom edge was sealed by water. At 0, 5, 10, 20, and 30 min after chamber closure, gas samples were extracted using 60 mL plastic syringes and immediately injected into 50 mL pre-evacuated Exetainer (Chen et al. 2014; Hou et al. 2001).
The N2O concentration was determined using the gas chromatograph method (Zou et al. 2005), which was performed with a modified gas chromatograph (Agilent 7890, Agilent Technologies) equipped with an electron capture detector (ECD) (Liu et al. 2012; Zou et al. 2005). Each pile along its length was sub-divided into three sections that were treated as three parallel locations to minimize spatial heterogeneity of gas and compost sampling. The N2O fluxes were calculated by a non-linear approach and the mean of fluxes taken from three parallel sections within each windrow represent flux measurement of the sampling windrows. Average fluxes and standard deviations of N2O were calculated from three replicated windrows. The cumulative N2O emissions were sequentially accumulated from the emissions between every two adjacent intervals of the measurements (Zou et al. 2005).
Physicochemical parameters determination
Windrow temperature at 30 cm depth of piles was measured using a mercury thermometer on each gas sampling day. To examine dynamics of physiochemical parameters and functional microbial abundance, the compost samples were randomly collected from three longitudinal locations from different parts of piles. The collected samples were divided into three parts. Two parts were immediately preserved at 4 °C or −80 °C, while the other part was air-dried, sieved, and stored for further analysis. The moisture content of different fresh samples was determined based on the weight loss by oven-drying at 105 °C. To analyze the water-soluble fractions of the compost material, the mixture of 20 g fresh compost samples with 200 mL deionized water (1:10 w/v ratio) was shaken on a horizontal shaker at 25 °C (Castaldi et al. 2008). To determine the NH4 + and NO3 − concentration of compost samples, 5 g of fresh samples were extracted with 100 mL 2 M KCl solution (1:20 w/v ratio) at room temperature. The solutions were measured using the three wavelength ultraviolet spectrometry by an ultraviolet spectrophotometer (HITACHI, U-2900, Japan).
DNA was extracted from the compost samples using the Ultraclean soil DNA isolation kit (MoBio, USA), as described in the manufacturer’s instructions. Each DNA sample for next-analysis was the mixture of three independent DNA extractions from one compost sample. The DNA sample concentration was determined by a Nanodrop (Thermo Scientific, USA).
Real-time q-PCR assay
The primers used for quantitative PCR in this study
Product size (bp)
30 s-95 °C,
95 °C-15 s, 55 °C-30 s, 72 °C-30 s,
80 °C-30 s
Henry et al. (2004)
95 °C-5 s, 58 °C-34 s, 72 °C-15 s 95 °C-15 s, 55 °C-30 s, 72 °C-30 s, 80 °C-30 s
30 s-95 °C,
80 °C-30 s
Scala and Kerkhof (1998)
95 °C-5 s, 60 °C-34 s, 72 °C-15 s 95 °C-15 s, 55 °C-30 s, 72 °C-30 s,
80 °C-30 s
30 s-95 °C,
Zhou et al. (2011)
95 °C-5 s, 55 °C-34 s, 72 °C-15 s 95 °C-15 s, 55 °C-30 s,72 °C-30 s, 80 °C-30 s
The q-PCR assays was carried out in 20 μL reaction volume containing 10 μL SYBR Premix ExTaq, 0.4 μL each primer (10 μmol−1), 0.4 μL ROX reference dye II (50×), 2 μL template DNA and 6.8 μL sterlized water. Reactions were perfomed triplicate using 7500 system (Appled Biosytem, USA). The information of primers and q-PCR reaction process was listed in Table 1. Target gene copy numbers in compost samples were calculated from the standard curves and dry weight of compost samples.
All data were reported as means and standard deviations. The pairwise correlation was conducted for the correlation between N2O fluxes, functional gene abundance (nirK and nosZ), and related physiochemical parameters (temperature, moisture, NH4 +, NO3 −). A linear model with the personality of ordinary least squares (OLS) was used to fit the N2O fluxes by physiochemical parameters and related functional gene abundance. All statistical analyses were performed using JMP version 9.0 (SAS Institute, USA, 2010).
The concentration of NH4 + and NO3 − during the composting process
NO3 − (mg/kg)
1026.45 ± 156.30
1150.39 ± 123.72
143.08 ± 21.95
151.68 ± 16.33
608.99 ± 89.77
552.07 ± 89.23
179.55 ± 17.40
205.35 ± 36.72
547.95 ± 101.23
580.66 ± 78.01
182.57 ± 29.80
192.59 ± 9.70
568.46 ± 45.89
552.64 ± 46.93
157.66 ± 31.90
175.10 ± 23.89
558.96 ± 56.11
580.70 ± 23.43
141.73 ± 10.91
168.62 ± 30.01
498.31 ± 30.03
573.46 ± 92.10
247.79 ± 27.18
177.87 ± 29.55
415.75 ± 56.30
544.38 ± 64.02
345.26 ± 38.45
218.10 ± 48.74
113.93 ± 19.78
212.17 ± 59.30
593.70 ± 68.29
541.83 ± 83.29
125.02 ± 34.04
288.12 ± 32.91
591.53 ± 56.48
503.60 ± 76.20
Abundance dynamics of denitrifying bacteria community
Correlations of N2O fluxes with gene abundance and physiochemical parameters
As recognized as an importance source of CH4 and N2O, manure composting has gained extensive attention of developing available strategies for alleviating GHG emissions (Chadwick et al. 2011; Owen and Silver 2015; Tsutsui et al. 2013). In this study, primary N2O fluxes were observed at middle stage of the composting in both piles (after 26 days), mainly because of the decreased temperature and limited oxygen availability. The fluxes of N2O in this study have also been supported by numerous previous relevant studies (Sanchez-Monedero et al. 2010; Tsutsui et al. 2013; Wang et al. 2013). Importantly, biochar amendment effectively reduced the N2O fluxes during the manure composting by 54.1 % as compared with the control piles, especially after the cooling stage from 34 days after treatment (Figs. 1, 2), suggesting its potential of application in agricultural production for migrating GHG emissions.
Previous studies have highlighted the positive performance of biochar on reduction of N2O emissions in both composting and soil systems. The involved mechanisms have been summarized as physical absorption, improved soil aeration (Zhang et al. 2010), mediation of denitrifiers (Wang et al. 2013), repressing denitrification and inducing N2O-reductase activities (Yanai et al. 2007), and regulating of N transformations (Clough and Condron 2010). Recently, it has been recognized that the N2O emissions during manure composting were the balance between production (NO3 − → N2O, primarily catalyzed by nitrite reductase encoding by nirS/nirK) and consumption (N2O → N2, catalyzed by nitrite reductase encoding by nosZ) (Maeda et al. 2011). Since nirK has been suggested to be the dominant denitrification gene as compared with nirS in the composting system (Wang et al. 2013; Zhang et al. 2015), the abundance of nirK and nosZ was investigated for understanding the microbial mechanisms that involved in the biochar-mediated N2O mitigation. As expected, addition of biochar counteracted the significant raise of nirK abundance as compared with the control pile, especially on day 34 at which the N2O emissions reached peak in the control piles in contrast to much lower N2O fluxes in the biochar-amended piles (Figs. 1, 6a). Moreover, the population of nosZ was found to be similar in both piles (Fig. 6b), therefore it could be hypothesized that the N2O reduced by biochar amendment was mainly attributed to the alternation of bacterial gene abundance of nirK. Previous studies also highlighted that biochar application could lowered the abundance of nirK in manure composting (Wang et al. 2013), and nirS (or relative proportion) under field condition (Anderson et al. 2014; Bai et al. 2015).
There are several probable explanations for the effects of biochar amendment on denitrification gene abundance. First, improvement of soil aeration by biochar amendment due to its nano-porosity and large specific surface areas, as well as the consequent lower moisture content (Fig. 4), could influence the oxygen availability and redox condition, thereby depress the abundance, diversity, and activity of the denitrifiers (Wang et al. 2013; Zhang et al. 2010). Second, ethylene generated from biochar could inhibit the abundance and activity of soil microbiota (Spokas et al. 2010). Nevertheless, additional studies are highly needed to exploring the detailed response mechanisms of denitrifier as responses to biochar amendment.
Applicable schematic model for predication of N2O fluxes is necessary for estimating the GHGs emission under various biogeochemical parameters, and could offer potential implications for GHGs mitigation. Currently, most of the developed N2O models were associated with physicochemical characteristics (e.g., pH, water content, oxygen level, climatic information, nitrogen inputs, etc.) or potential denitrification/nitrification rates (Hu et al. 2015). However, limitations of these models in predication of N2O emissions in different circumstances have also been marked, and there is an urgent demand to exploit novel N2O emission models on account of nitrogen-cycling microbes or indicator genes determined by molecular strategies (Wallenstein and Hall 2011). In this study, the significant correlation between N2O fluxes and bacterial denitrification genes population, as well as nirK-nosZ value (Fig. 6a, b) was supported by previous studies (Wang et al. 2013). The derived linear regression model based on nirK-nosZ value could explain 80 % of the variance in N2O fluxes during windrow composting, which was similar to the model raised recently using nirS-nosZ value as the proxy (Morales et al. 2010). A previous field study also highlighted the linear correlation between nirS-nosZ value and N2O fluxes (Morales et al. 2010). It has been documented that nitrite reductase encoded by nirS was predominate as compared with nirK in most natural environments (Bothe et al. 2000), while it seemed that nirK gene was more dominant in composting systems (Wang et al. 2013). Furthermore, we developed a modified model for predicting of the N2O fluxes associated with the detailed abundances of denitrification functional genes (nirK and nosZ) during the manure composting (Fig. 7). The higher explaining fitting of this model (explaining 88 % of the variance in N2O fluxes) as compared with the linear model suggested that this linear equation was more effective in predicating N2O fluxes during composting based on the abundance of relevant functional genes (Fig. 7). This model highlighted the significant roles of denitrification in N2O emissions, which was the balance between N2O production (catalyzed by nirK) and consumption (catalyzed by nosZ) (Maeda et al. 2011; Wang et al. 2013).
Biochar amendment could also alleviate the N2O emissions through other ways independent of bacteria. For example, metal oxides, such as TiO2 distributing near the biochar, could catalyze the reduction of N2O to N2 (Ovideo and Sanz 2005). Moreover, the concentration of NO3 − was observed to be significantly lower in the biochar-amended piles than in the control piles, which could also have reduced N2O fluxes. However, whether the reduced NO3 − was directly attributed to the biochar amendment or indirectly caused by the effect of biochar on microbial metabolism still needs further investigation.
Besides of the mitigation effects on N2O emissions, biochar amendment also revealed other positive effects on manure composting. It was observed that addition of biochar accelerated the temperature rising and prolong the thermal stage of the composting (Fig. 3), which could improve the degradation of the organic substrates and shorten the composting period. This phenomenon has also been reported previously, and the involved mechanisms might be improvements of aeration and nutrients brought by the biochar (Wang et al. 2013).
In conclusion, this research presented that biochar amendment significantly reduced N2O emissions from manure composing, primarily through alternation of abundance of denitrification genes (nirK). Our study also highlighted the significant positive correlation between nirK-nosZ value and N2O fluxes, and developed a schematic model for predicting of the N2O fluxes associated with denitrification functional genes. It should be noticed that compared with advanced strategies such as next-generation sequencing and transcriptional profiling analysis, q-PCR has limitations both on data size and reliability (activity in vivo). Therefore, in the future more available approaches should be used for deeply exploring the microbial process involved in the biochar-mediated mitigation, especially in the detailed response of denitrification groups to biochar.
Experiment planning and design: Shuqing Li, SL, JZ, and QS; Sampling collection and analysis: LS, YJ; Paper construction: Shuqing Li, SL, and JZ. All authors read and approved the final manuscript.
This work was supported by the National Basic Research Program of China (2015CB150502), National Natural Science Foundation of China (NSFC 41225003, 41401321), and Ministry of Education 111 project (B12009).
The authors declare that they have no competing interests.
This article does not contain studies with human participant or animals performed by any of the authors.
Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.
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