Investigating microbial metabolic characteristics and soil organic carbon (SOC) within aggregates and their relationships under conservation tillage may be useful in revealing the mechanism of SOC sequestration in conservation tillage systems. However, limited studies have been conducted to investigate the relationship between SOC and microbial metabolic characteristics within aggregate fractions under conservation tillage. We hypothesized that close relationships can exist between SOC and microbial metabolic characteristics within aggregates under conservation tillage. In this study, a field experiment was conducted from June 2011 to June 2013 following a split-plot design of a randomized complete block with tillage practices [conventional intensive tillage (CT) and no tillage (NT)] as main plots and straw returning methods [preceding crop residue returning (S, 2100−2500 kg C ha−1) and removal (NS, 0 kg C ha-1)] as subplots with three replications. The objective of this study was to reveal the effects of tillage practices and residue-returning methods on topsoil microbial metabolic characteristics and organic carbon (SOC) fractions within aggregates and their relationships under a rice–wheat cropping system in central China. Microbial metabolic characteristics investigated using the Biolog system was examined within two aggregate fractions (>0.25 and <0.25 mm). NT treatments significantly increased SOC concentration of bulk soil, >0.25 aggregate, and <0.25 mm aggregate in the 0−5 cm soil layer by 5.8%, 6.8% and 7.9% relative to CT treatments, respectively. S treatments had higher SOC concentration of bulk soil (12.9%), >0.25 mm aggregate (11.3%), and <0.25 mm aggregate (14.1%) than NS treatments. Compared with CT treatments, NT treatments increased MBC by 11.2%, 11.5%, and 20%, and dissolved organic carbon (DOC) concentration by 15.5%, 29.5%, and 14.1% of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate in the 0−5 cm soil layer, respectively. Compared with NS treatments, S treatments significantly increased MBC by 29.8%, 30.2%, and 24.1%, and DOC concentration by 23.2%, 25.0%, and 37.5% of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate in the 0−5 cm soil layer, respectively. Conservation tillage (NT and S) increased microbial metabolic activities and Shannon index in >0.25 and <0.25 mm aggregates in the 0−5 cm soil layer. Redundancy analysis showed that the SOC and its fractions (DOC and MBC) were closely correlated with microbial metabolic activities. Structural equation modelling showed that the increase in microbial metabolic activities directly improved SOC by promoting DOC in >0.25 mm aggregate in the upper (0−5 cm) soil layer under conservation tillage systems, as well as directly and indirectly by promoting DOC and MBC in <0.25 mm aggregate. Our results suggested that conservation tillage increased SOC in aggregates in the topsoil by improving microbial metabolic activities.
Citation: Guo L-J, Lin S, Liu T-Q, Cao C-G, Li C-F (2016) Effects of Conservation Tillage on Topsoil Microbial Metabolic Characteristics and Organic Carbon within Aggregates under a Rice (Oryza sativa L.) –Wheat (Triticum aestivum L.) Cropping System in Central China. PLoS ONE 11(1): e0146145. https://doi.org/10.1371/journal.pone.0146145
Editor: Wenju Liang, Chinese Academy of Sciences, CHINA
Received: November 1, 2015; Accepted: December 13, 2015; Published: January 5, 2016
Copyright: © 2016 Guo et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited
Data Availability: All relevant data are within the paper and its Supporting Information files.
Funding: Dr. Cheng-Fang Li was financially supported by the National Natural Science Foundation of China (31471454), Fundamental Research Funds for the Central Universities (2013PY106) and Major Scientific and Technological Innovation Projects in Hubei Province (2014ABA027), Dr. Shan Lin by the National Natural Science Foundation of China (41201255), Dr. Cou-Gui Cao by National Technology Project for High Food Yield of China (2011BAD16B02), and Li-Jin Guo by Huazhong Agricultural University Independent Scientific & Technological Innovation Foundation (2014bs02). The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Anthropogenic carbon dioxide (CO2) emissions into the atmosphere have increased significantly by 39% from 6.3 Gt C in 1994 to 8.7 Gt C in 2009 . Reducing CO2 concentration to mitigate global climate change by carbon (C) sequestration has been a promising method . Considerable attention has been given to the dynamics of soil organic C (SOC) stocks and its function in long-term C accumulation and sequestration of atmospheric CO2 for mitigating climate change, maintaining crop productivity sustainability, and increasing soil fertility . Reasonable management practices, such as no tillage (NT) and residue returning (S), facilitate SOC sequestration in croplands .
Agricultural SOC accumulation is influenced by numerous factors, such as tillage practices [4,5], soil aggregate size [4,6], and microbial functional diversity [7,8]. Tillage practices can affect the stability or composition of SOC [4,6], and thus affect SOC concentration and SOC density of the plough layer . Conventional intensive tillage (CT) can decrease soil aggregate stability and accelerate soil organic matter oxidation , thereby threatening sustainable crop production . Sustainable soil management can be achieved through conservation tillage practices, including NT and crop residue returning . Conservation tillage significantly reduces soil physical disturbance , promotes soil aggregation, and improves soil microorganism dynamics because of more beneficial environmental conditions [13,14]. Therefore, investigating the effects of conservation tillage on SOC is necessary for further understanding soil sequestration.
Soil aggregates that control the dynamics of soil organic matter and nutrient cycling are structural units within the soil . The aggregate hierarchy model shows that soil C accumulation in a given system may comprise a hierarchy of biological processes at the spatial dimension of soil physical structure [16,17]. Ettema and Wardle  reported that soil biota should be recognized at different spatial scales to understand their functions better in the ecosystem. Zhang et al.  also reported that previous studies mainly focused on the effects of microorganisms on the vertical and horizontal orientations of soil profiles and ignored the effects on the micro-spatial dimension of soil physical structure. Therefore, investigation of SOC driven by soil microbial community processes within soil aggregates will help elucidate the regulation of soil biota in soil C storage.
Soil microorganisms significantly affect the health of an agroecosystem through their functions in residue decomposition and nutrient cycling, as well as their associations with other organisms . The activities and compositions of soil microbial community and their interactions with environmental factors affect SOC dynamics and crop productivity [19,20]. Direct mmeasurements of metabolic diversity of soil microbial communities are likely to provide more relevant information regarding soil functions compared with measurements of species diversity  because soil microorganisms generally present in resting or dormant stages, in which they are not functionally active . Biolog system, a rapid community-level approach for assessing patterns of sole C source utilization, is used to study microbial community metabolic activities [22,23]. Several studies used the Biolog system to differentiate microbial communities from diverse habitats [22,23]. However, only a few these studies determined the relationship between soil microbial metabolic activities and SOC, especially within aggregates, in rice–wheat cropping systems.
Rice–wheat cropping systems possess important functions in food security in Asia by providing food grains for more than 20% of the population worldwide [24,25]. Central China comprises the main production region of rice and wheat in China. In this region, the planting area of the system occupies approximately 16% of the total planting area of both crops . The effects of conservation tillage on rice–wheat cropping systems are well demonstrated [14,25]. However, limited attention has been given to the relationship between SOC and microbial metabolic characteristics within aggregate fractions under conservation tillage in the rice–wheat system. Thus, we hypothesized that (1) microbial metabolic activity is improved by conservation tillage at the small-scale in soil in the plow layer, and (2) the microbial metabolic activity is correlated to SOC within aggregates under conservation tillage. So, this study aimed to assess the effects of tillage practices (i.e., NT and CT) and straw returning methods (i.e., preceding crop residue removal and returning) on microbial metabolic characteristics and SOC within aggregates and their relationships under a rice–wheat cropping system in central China. To test our hypotheses, structural equation modelling (SEM) was used to detect potential associations among tillage systems (straw systems), microbial metabolic activities, organic C fractions, and SOC to elucidate the relationship better between soil microbial metabolic diversity and SOC within aggregates.
Materials and Methods
The experimental site was located at the Huazhong Agricultural University Research Farm of Huaqiao Town in Wuxue City, Hubei Province, China (E29° 51′N, 115° 33′E), which belongs to Extend Service Center of Agricultural Technonlogy of Wuxue Agricultural Bureau, Hubei Province. This study was performed in cooperation with Huazhong Agricultural University and Extend Service Center of Agricultural Technonlogy of Wuxue Agricultural Bureau, Hubei Province. The farm operations of this experiment were similar to local farmers’ operations and the field experiment did not involve endangered or protected species. This experiment was approved by College of Plant Science and Technology, Huazhong Agricultural University and Extend Service Center of Agricultural Technonlogy of Wuxue Agricultural Bureau, Hubei Province.
This site has a humid mid-subtropical monsoon climate with an average annual temperature of 17.8°C and an annual precipitation of 1361 mm, with most of the rainfall occurring between April and August. The paddy soil of the site is a silty clay loam classified as Gleysol (FAO classification) . The main soil properties (0−20 cm depth) are as follows: pH 4.79; organic C, 16.89 g kg−1; total nitrogen (N), 2.20 g kg−1; total phosphorus (P), 0.45 g kg−1; and bulk density, 1.21 g cm−3. The experimental site was cultivated with a cropping system of rice (Huanaghuazhan, Oryza sativa L.) and wheat (Zhengmai 9023, Triticum aestivum L.). Rice seedlings were thrown in June, and grains were harvested in October each year. Wheat was directly seeded in October, and grains were harvested in June the following year.
Field treatment was initiated in June 2011 following a split-plot design of a randomized complete block and with tillage practices (CT and NT) as main plots and straw returning methods [preceding crop straw removal (NS) and return (S)] as subplots. The experiment comprised four treatments, namely, CTNS, CTS, NTNS and NTS. Each treatment had three replications. Each sub-plot has an area of 90 m2. For CTNS and NTNS treatments, preceding crop residues were removed and were not returned to the field. For CTS and NTS treatments, preceding crop residues were chopped to approximately 5−7 cm in length. The chopped residues were subsequently mulched in soil for NT and incorporated into soil for CT. CT treatment was moldboard ploughed twice to a 20 cm depth before throwing of rice seedlings and once before sowing of wheat. Soil disturbance was not conducted for NT treatments. The C/N ratios of wheat and rice residues used were about 46 and 71, respectively.
Weeds were controlled by spraying 36% glyphosate at 3 L ha−1. Rice seedlings were manually thrown at a density of 190,000 seedlings ha−1 in June, and grains were harvested in October each year. Wheat was directly seeded at 150 kg ha−1 in October of each year, and grains were harvested manually in June the following year. The fields were moist because conventional irrigation–drainage practices were followed. However, these fields were non-waterlogged through intermittent irrigation (irrigated every three days to five days) during the rice growing season, except during tillering and maturing stages. Irrigation was not provided during the wheat growing season.
Fertilizers were broadcasted during crop-growing season, with rice receiving 180 kg N ha−1, 90 kg P2O5 ha−1, and 180 kg K2O ha−1, and wheat receiving 144 kg N ha−1, 72 kg P2O5 ha−1, and 144 kg K2O ha−1. During rice-growing seasons, N fertilizer was applied in four splits: 50% N (as 46% urea) was used as basal N, 20% at the mid-tillering stage, 12% at the jointing stage, and 18% at the earring stage. During wheat-growing seasons, N fertilizer was applied in three splits: 50% N was used as basal N, 30% at the tillering stage, and 20% at the boosting stage. Both P (as single superphosphate, 16% P2O5) and K (as potassium chloride, 60% K2O) fertilizers were merely applied as basal fertilizers immediately after throwing rice seedlings or sowing wheat.
Soil sampling and analysis
Soil cores from between rows in each plot were collected immediately after wheat harvest in June 2013 using a soil core sampler (inner diameter = 7 cm) at random. Samples consisted of eight composite soil cores sectioned into 0−5 cm, 5−15 cm and 15−20 cm depth increments. After sampling, visible plant residues and stones were removed, and large soil clods were gently broken by hand. Soils were then sieved through a 5-mm screen for uniformity. Aggregates were separated following the dry-sieving method described by Gartzia-Bengoetxea et al. . A total of 100 g (<5 mm) of air-dried soil fragments were placed in a nest of sieves mounted on Retsch AS200 Control (Retsch Technology, Düsseldorf, Germany). Sieves were mechanically shaken (amplitude = 1.5 mm) for 2 min to separate soil into >0.25 and <0.25 mm aggregates. The SOC concentration of aggregate fractions was determined using a FlashEA 1112 elemental analyzer (Thermo Finnigan, Italy).
Soil microbial biomass C (MBC) was determined via fumigation–extraction method . Both fumigated and non-fumigated soils were extracted with 0.5 M K2SO4 for 30 min, and organic C in the soil extract was measured through oxidation with potassium dichromate and titration with ferrous ammonium sulfate . MBC was calculated as EC/KEC, where EC is the difference of organic C extracted from the fumigated and non-fumigated soil, and KEC is 0.38.
Dissolved organic C (DOC) was determined as described by Jiang et al. . Fresh field soil (equivalent to a 10-g oven-dry weight, 1:2.5 ratio) was shaken with water at 250 r min−1 for 30 min at 25°C and then centrifuged at 4,500 rpm min-1 for 10 min. The supernatant was collected and filtered with a 45-μm membrane filter. The DOC of the filtrate was analyzed through oxidation with potassium dichromate and titration with ferrous ammonium sulfate .
Biolog analysis of soil
The metabolic characteristics of soil microbial communities were measured using ECO Biolog system microplates (Biolog Inc. Hayward, CA), which were used to determine the C source utilization pattern. The 96-well ECO microplate comprised three replicate wells, each replicate comprised 31 C substrates and a control well without C substrates. The substrates were carbohydrates (n = 12), amino acids (n = 6), carboxylic acids (n = 5), polymers (n = 4), phenolic compounds (n = 2), and amines (n = 2). Fresh soil samples weighing 1 g each were shaken in 99 ml of sterile saline water (0.85% NaCl w/v) for 30 min. The mixtures were then diluted to a final dilution of 10−3 in the plates. The plates were incubated at 25°C in the dark, and absorbance readings at 590 nm were determined at 0 h and every 12 h thereafter up to 168 h by using a microplate reader (ELISA reaction plate reader). An average well color development (AWCD) was calculated to determine the rate of color development on Biolog plates for each plate at each reading . Data at 96 h were used to calculate AWCD. Shannon index was calculated to evaluate microbial metabolic diversity. This index was calculated as follows: H = −∑[pi×ln(pi)], where pi is the ratio of activities on each substrate to the sum of activities on all substrates .
All data were analyzed with SAS 9.0 (SAS institute, 1990). The data sets were analyzed as a split-plot design with tillage treatment as the main factor and residue returning as sub-factor. Normality of the residuals was tested with the Shapiro-Wilk test and homogeneity of variances with Levene’s test. Two-way ANOVA was conducted to analyze the effects of tillage, straw returning and their interactions on microbial metabolic activity, SOC, DOC and MBC within aggregates. Duncan's multiple range tests were performed to examine whether the differences between the mean values were statistically significant at a significance level of 0.05. Redundancy analysis was performed using CANOCO software to explain the relationship between SOC and microbial metabolic diversity. Grace et al.  emphasized that SEM is an advanced and robust multivariate statistical method that allows hypothesis testing of complex path-relation networks. In the present study, SEM was used to evaluate whether soil microbial metabolic diversity has significant effects on SOC in response to the conversion of non-conservation tillage to conservation tillage. A priori model was constructed according to a literature review and our knowledge of how these predicators are related. Tillage systems (Tillage), straw systems (Straw), Shannon index, DOC, MBC, and SOC were the predicators in the initial model. In the model, microbial metabolic diversity was represented by Shannon index. The analysis was performed with AMOS 7.0 software  using the ‘robust’ maximum likelihood estimation procedures. Several tests were used to assess model fit, i.e. the χ2-test, comparative fit index (CFI), goodness-of-fit (GFI) and root square mean error of approximation (RMSEA).
Compared with CT treatments, NT treatments did not affect SOC concentration of bulk soil in the 5−20 cm soil layer, but significantly increased the SOC concentration of bulk soil in the 0−5 cm soil layer (Table 1). In comparison with NS treatments, S treatments had not significant effects on SOC concentration of bulk soil in the 5−20 cm soil layer, but significantly enhanced the SOC concentration of bulk soil in the 0−5 cm soil layer (Table 1). Therefore, this study only investigated the effects of conservation tillage on microbial metabolic characteristics and the relationships between the metabolic characteristics and SOC within aggregates in the 0−5 cm soil layer.
In the 0−5 cm soil layer, NT treatments significantly increased SOC concentration by 5.8%, 6.8%, and 7.9% of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate, respectively, compared with CT treatments (Table 1). NT treatments significantly increased MBC of bulk soil, >0.25 mm and <0.25 mm aggregates by 11.2%, 11.5% and 20.0%, respectively, compared with CT treatments. DOC concentrations of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate under NT treatments were 15.5%, 29.5%, and 14.1% higher than those under CT treatments, respectively. In comparison with NS treatments, S treatments significantly increased SOC concentrations of bulk soil by 12.8%, >0.25 mm aggregate by 11.3%, and <0.25 mm aggregate by 14.1%. In addition, MBC of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate under S treatments were 29.8%, 30.2%, and 24.1% higher than those of NS treatments, respectively. S treatments exhibited 25.0%, 37.5%, and 23.2% higher DOC concentrations of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate compared with NS treatments, respectively. In the 0−5 cm soil layer, there were significant interactions of tillage and straw returning on SOC concentration of >0.25 mm and <0.25 mm aggregates, MBC of bulk soil and <0.25 mm aggregate, and DOC concentration of >0.25 mm aggregate.
Biolog substrate metabolic activities
Carbon (C) substrates tested using Biolog were categorized into six groups, namely, carbohydrates, amino acids, carboxylic acids, polymers, phenolic compounds, and amines (Table 2). Microbial metabolic activities varied among different treatments and aggregate fractions. Conservation tillage significantly increased microbial metabolic activities in both >0.25 and <0.25 mm aggregates. Compared with CT treatments, NT treatments significantly increased AWCD and Shannon index by 20.0% and 1.1% in >0.25 mm aggregate and by 23.0% and 1.3% in <0.25 mm aggregate, respectively. Similarly, compared with NS treatments, S treatments significantly increased AWCD and Shannon index by 37.5% and 2.4% in >0.25 mm aggregate and by 35.5% and 2.9% in <0.25 mm aggregate, respectively. In generally, interactions of tillage and straw returning significantly affected soil microbial metabolic activities and Shannon index in >0.25 mm and <0.25 mm aggregates in the 0−5 cm soil layer.
Redundancy analysis shows that the coordinates from the first two ordination axes explained 97.0% (first axis, 91.6% and second axis, 5.4%) and 98.6% (first axis, 83.0% and second axis, 5.3%) of the variances in >0.25 mm (Fig 1A) and <0.053 mm aggregates (Fig 1B). Moreover, Monte Carlo permutation test showed that all SOC fractions (including SOC) significantly affected microbial substrate utilization pattern (P<0.05) in >0.25 and <0.25 mm aggregates. Overall, a clear separation was observed between treatments, and similar responses of SOC fractions (SOC, MBC, and DOC) within aggregates to microbial substrate utilization were found.
CTNS, conventional intensive tillage with straw removal; CTS, conventional intensive tillage with straw returning; NTNS, no-tillage with straw removal; tillage; NTS, no-tillage with straw returning. SOC, soil organic C; MBC, microbial biomass C; DOC, dissolved organic C; AWCD, an average well color development.
Relationship between soil microbial metabolic diversity and SOC under tillage and residue systems were analyzed separately using SEM for >0.25 and <0.25 mm aggregates (Fig 2). SEM revealed that the predictors explained 53% to 57% of the variation in SOC in >0.25 mm aggregate, and 62% to 73% in <0.25 mm aggregate. In >0.25 and <0.25 mm aggregates, microbial metabolic diversity affected SOC directly and indirectly through DOC and MBC, respectively. Moreover, changes in microbial metabolic diversity induced by tillage or straw systems influenced SOC directly through DOC in >0.25 mm aggregate, and directly and indirectly through DOC and MBC in <0.25 mm aggregate (Fig 2).
Rectangles represent observed variables. Arrow thickness represents the magnitude of the path coefficient. Values associated with solid arrows represent the path coefficients. Solid and dashed arrows indicate significant (P<0.05) and non-significant (P>0.05), respectively. Tillage, tillage systems; Straw, straw systems; DOC, dissolved organic C; MBC, microbial biomass C; SOC, soil organic C.
This study investigated the effects of conservation tillage on soil microbial metabolic activities and SOC within aggregate fractions and their relationships under a rice-wheat cropping system in central China. The results partly supported our hypothesis that conservation tillage could only improve microbial metabolic activities and SOC in the top soil layer (0–5 cm) after two cycles of annual rice–wheat rotation and close relationships could be found between SOC and microbial metabolic activities within aggregates in this layer.
Effects of conservation tillage on SOC, DOC, and MBC within aggregates
Conservation tillage generally increased SOC concentration of plow layer [10,35], which is probably because conservation tillage can reduce soil disturbance, promote root development in the topsoil, and increase crop residue accumulation on the soil surface, thus enhancing soil aggregate stability [9,10]. However, a number of studies reported no significant effects of conservation tillage on SOC [13,14]. Conservation tillage significantly increased SOC concentration of bulk soil in the 0−5 cm soil layer in this study (Table 1). This increase in SOC concentration can be attributed to a combination of less soil disturbance and more residues returned to the soil surface under conservation tillage [36,37]. Triberti et al.  reported that crop residues can significantly increase SOC concentration. Dikgwatlhe et al.  also reported similar results wherein conservation tillage increased SOC concentration in the 0−5 cm top soil. They suggested that the increase may be due to the lack of residues incorporated to soil and intensive soil tillage that accelerated soil organic matter decomposition. Alvarez et al.  found that NT increases SOC and total N concentrations in the first centimeters of the soil profile because NT maintains surface residues. However, similar results were not observed in the 5−20 cm soil layer (Table 1). The return of higher residues and root biomass to the soil surface instead of migrating into deeper soil under NT [36,40,41], weakening the effects of NT on the SOC content in the plow layer . Although crop residues were incorporated into the plow layer in CTS treatment, soil disturbance would greatly decrease abundance and diversity of soil microorganisms [13,14], thus reducing decomposition of the residue incorporated into the deeper layer (5–20 cm). Therefore, no significant increases in SOC were found in the 5–20 cm soil layer among treatments.
In this study, SOC concentration was higher under >0.25 mm aggregate than that under <0.25 mm aggregate in the 0−5 cm soil layer (Table 1). Higher SOC concentrations generally are observed in macroaggregates than in microaggregates [42,43]. The conceptual model for aggregate hierarchy indicated that the increase in SOC concentration with increasing aggregate size is possibly caused by the macroaggregates, which are composed of the microaggregates plus organic binding agents . The macroaggregates can provide better protection mechanism for soil organic matter than microaggregates [42,43]. Furthermore, higher SOC concentrations of >0.25 and <0.25 mm aggregates were observed under S treatments than under NS treatments, and under NT treatments than under CT treatments (Table 1). Madejon et al.  reported that soil biological activity under NT can promote the production of organic binding by-products that stabilize soil aggregates. Fresh and labile pools of organic matter cause rapid stimulation of soil microorganisms, accompanied by a significant increase in macroaggregate formation . Zhao et al.  found that the majority of the increases in SOC under NT occur in macroaggregates. Moreover, NT and crop residue returning tend to reduce the turnover rate of macroaggregates , thus resulting in SOC accumulation in the soil surface. Jiang et al.  also reported that conservation tillage (NT and residue returning) promotes accumulation of macroaggregate-protected C.
In the current study, higher DOC and MBC of bulk soil, >0.25 mm aggregate, and <0.25 mm aggregate were observed under conservation tillage in the 0−5 cm soil layer (Table 1). Such increase may be attributed to higher organic matter inputs and improved environmental conditions for soil microbial community under conservation tillage .
Effects of conservation tillage on soil microbial metabolic activities within aggregates
Nannipieri et al.  suggested that the activity and diversity of microorganisms determine the stability and function of soil ecosystems. Although the BIOLOG system has been criticized for being a cultivation-based method that considers only a fraction of all microbial species in soil [22,23], the system is widely used because it is an efficient method to reveal soil microbial C substrate metabolic activity [20,21]. Various studies have employed the microbial metabolic method to differentiate microbial communities among diverse habitats and examine the natural variation and diversity of microbial communities , which offers opportunities in monitoring changes in microbial diversity caused by different management practices . Bending et al.  reported that soil management practices exhibit considerable influence on the structure and metabolic diversity of soil microorganisms. Garbeva et al.  found that residue quantity, quality, environmental conditions, and their complex interactions significantly affect soil microbial functional diversity.
Results of the present study showed that the Biolog system can reveal differences in microbial substrate utilization between treatments (Table 2). Conservation tillage significantly increased microbial substrate utilization (including amino acids, carboxylic acids, polymers, phenolic compounds, and carbohydrates) of >0.25 and <0.25 mm aggregates. This result suggests that conservation tillage can provide higher SOC availability from the decomposition of fresh organic inputs on the soil surface to soil microorganisms as suggested by Baker et al. . Such findings are supported by high MBC and DOC under conservation tillage (Table 1). Moreover, conservation tillage improved soil microbial activity on the soil surface. Improvement in microbial activity leads to increased production of organic binding by-products from the decomposition of fresh organic residues that contributes to the presence of microaggregates and organic bindings that comprise macroaggregates [47,53]. Conservation tillage can also provide beneficial environmental conditions for soil microbial community through accumulating residues on the top soil layer and less fluctuation in soil water content and temperature [4,13]. Furthermore, conservation tillage can promote root development on the topsoil [54,55], thus providing high availability of organic C sources for soil microorganisms.
Shannon index reveals microbial species richness and evenness in terms of C component utilization . Higher Shannon index was observed in >0.25 and <0.25 mm aggregates in the upper soil layer under conservation tillage (Table 2). Several researchers suggested that conservation tillage increases soil microbial abundance and diversity from various geographical locations, agroecosystem types, and cropping years [13,57]. For instance, Wang et al.  found higher soil bacterial abundance and diversity under NT and S treatments than under CT. They also reported that NT plus 100% crop residue incorporation is the best agricultural strategy for improving soil microbial communities, which may be due to the decrease in soil temperature and water content fluctuation, as well as increase in organic matter and energy sources provided by NT and residue incorporation. Lupwayi et al.  observed that catabolic diversity of microbial communities is greater under NT than under CT through the Biolog system. However, Helgason et al.  found that the distribution pattern of soil biota within aggregates may be governed by aggregate size and not by tillage practices. The discrepancy of the results may be attributed to soil-specific properties, such as mineralogy, soil C and nutrient concentration, and differences in the methods used [59,60].
Relationship between SOC and microbial metabolic activities within aggregates under conservation tillage
Soil microbial communities possess important functions in SOC decomposition and C sequestration processes through metabolizing organic matter sources . SOC is highly correlated with soil microbial community . In this study, SOC was closely correlated with microbial substrate utilization (Fig 1). On one hand, SOC decomposition is controlled by the quality and availability of organic C resources utilized by microbial communities [13,19]. Several studies suggested that labile fractions (including MBC and DOC) are closely related to SOC dynamics [13,14]. On the other hand, soil microbial community and their interactions with the environment are important factors that affect SOC dynamics, and any change in soil microbial community may alter SOC availability .
A number of studies have reported that the distribution pattern of soil biota within aggregates may be governed by aggregate size . Aggregate size is closely correlated with pore space, which determines the fluxes of oxygen and water [4,15], thus affecting soil biota and their functions in C dynamics. Stewart et al.  reported that soil C sequestration capacity is mainly determined by the degree of SOC protection from decomposition provided by the spatially hierarchical organization of soil aggregate structure. In the current study, metabolic diversity affected SOC directly and indirectly through DOC and MBC of >0.25 and <0.25 mm aggregates in the topsoil (0−5 cm) (Fig 2). Moreover, microbial metabolic diversity influenced SOC directly through DOC in >0.25 mm aggregate, and directly and indirectly through DOC and MBC in <0.25 mm aggregate under tillage and straw systems. Soil microenvironment contributes to the heterogeneous distribution of microorganisms within aggregates , thus leading to different effects of microorganisms on SOC within aggregates. Macroaggregates exhibit faster turnover time than microaggregates  because macroaggregates are mainly formed through binding of microaggregates and organic amendments ; therefore, macroaggregates more easily obtain fresh organic matter. Choudhury et al.  also reported that straw returning results in the preponderance of macroaggregates compared with microaggregates caused by the formation of water-stable aggregates. The presence of more stable macroaggregates is the first condition required for C sequestration . Therefore, conservation tillage can be speculated to promote the accumulation of straws in the top soil layer (0−5 cm), which leads to rapid straw decomposition accompanied by microbial growth . This phenomenon improves soil microbial metabolic activities. Straw decomposition also increases the input of labile organic matter (such as DOC and particulate organic C) into the soil and promotes the formation of >0.25 mm aggregate , eventually affecting SOC.
Compared with macroaggregates, microaggregates exhibit lower C concentrations and longer turnover times . Aggregate size controls pore space of the aggregate, thus determining the fluxes of oxygen, water, and microhabitats for microbial biota [4,52]. Fungi reside in large pores of large macroaggregates because of relatively high aeration and SOC substrates [69,70]. By contrast, bacteria survive in microaggregates because microaggregates provide protective habitats for microorganisms through pore size exclusion of predators . Zhang et al.  reported microbial contribution to SOC within aggregates. They found that bacteria and fungi contributed to SOC in >1 mm aggregate, whereas only bacteria were relevant in <1 mm aggregate. Zhang et al.  reported that soil microbial communities promote the accumulation of C directly and indirectly through MBC, and the input level of microbial-derived C and MBC regulate SOC within aggregates. In the present study, microbial functional diversity affected SOC directly and indirectly through DOC and MBC in <0.25 mm aggregate under tillage and straw systems (Fig 2). Therefore, conservation tillage can be speculated to increase organic matter input, thus promoting bacterial growth in <0.25 mm aggregate and subsequently SOC.
Several studies have reported that conservation tillage can decrease soil bulk density and improve soil porosity, thus promoting root development in the topsoil [54,55]. The root system is a main source of organic C accumulation in the soil , which directly influences the soil aggregation state. Uren  suggested that microbial function is largely affected by the ability of microorganisms to degrade root exudates, which are composed of small organic molecules, such as carbonic acids, amino acids, and sugars. Different tillage and straw managements can cause differences in physical aeration of soil conditions and in the growth of roots and their subsequent distribution . This phenomenon leads to differences in plant root exudates within aggregate fractions and subsequently SOC. Baker et al.  also suggested that tillage practices can change soil environmental conditions, which affect root growth and C and N mineralization. Soil microbial community can respond quickly to the change , thus leading to shifts in soil microbial community components and microbial metabolic activities.
After two cycles of annual rice–wheat rotation, results of the present study indicate that conservation tillage did not affect SOC in the plow layer (0−20 cm) but improved microbial metabolic activities and SOC in the upper (0−5 cm) soil profile. Close relationships between microbial metabolic activities and SOC within aggregates in the top soil layer. Results of SEM revealed that conservation tillage improved microbial metabolic diversity in the upper soil layer, thus increasing SOC of aggregates.
Conceived and designed the experiments: CFL. Performed the experiments: LJG SL. Analyzed the data: LJG SL CFL. Contributed reagents/materials/analysis tools: TQL CGC. Wrote the paper: LJG SL.
- 1. Boden T, Andres B, Marland G (2013) Ranking of the World's Countries by 2009 Total CO2 Emissions from Fossil-fuel Burning, Cement Production, and Gas Flaring. Carbon Dioxide Information Analysis Center. http://cdiac.ornl.gov/trends/emis/top2009.tot.
- 2. Zhu LQ, Li J, Tao BT, Hu NJ (2015) Effect of different fertilization modes on soil organic carbon sequestration in paddy fields in South China: a meta-analysis. Ecological Indicators 53:144–153.
- 3. Srinivasarao C, Venkateswarlu B, Lal R, Singh AK, Vittal KPR, Kundu S, et al. (2012) Long-term effects of soil fertility management on carbon sequestration in a rice–lentil cropping system of the Indo-Gangetic plains. Soil Science Society of America Journal 76:168–178.
- 4. Zhang S, Li Q, Lü Y, Zhang X, Liang W (2013) Contributions of soil biota to C sequestration varied with aggregate fractions under different tillage systems. Soil Biology & Biochemistry 62:147–156.
- 5. Liu C, Lu M, Cui J, Li B, Fang C (2014) Effects of straw carbon input on carbon dynamics in agricultural soils: a metaanalysis. Global Change Biology 20:1366–1381. pmid:24395454
- 6. Devine S, Markewitz D, Hendrix P, Coleman D (2014) Soil aggregates and associated organic matter under conventional tillage, no-tillage, and forest succession after three decades. Plos One 9:e84988. pmid:24465460
- 7. Stirling FR, Moody PW, Stirling AM (2010) The impact of an improved sugarcane farming system on chemical, biochemical and biological properties associated with soil health. Applied Soil Ecology 46:470–477.
- 8. Pritchett K, Kennedy AC, Cogger CG (2011) Management effects on soil quality in organic vegetable systems in western Washington. Soil Science Society of America Journal 75:605–615.
- 9. Gathala MK, Ladha JK, Saharawat YS, Kumar V, Sharma PK (2011) Effect of tillage and crop establishment methods on physical properties of a medium-textured soil under a seven-year rice-wheat rotation. Soil Water management conservation. Soil Science Society of America Journal 75:851–1862.
- 10. Mathew RP, Yu CF, Githinji L, Githinji L, Ankumah R, Balkcom KS (2012) Impact of no-tillage and conventional tillage systems on soil microbial communities. Applied and Environmental Soil Science
- 11. Hobbs PR, Sayre K, Gupta R (2008) The role of conservation agriculture in sustainable agriculture. Philosophical Transactions of the Royal Society B 363:543–555.
- 12. Uri ND (1999) Factors affecting the use of conservation tillage in the United States. Water, Air, and Soil Pollution 116:621–638.
- 13. Helgason BL, Walley FL, Germida JJ (2010) Long-term no-till management affects microbial biomass but not community composition in Canadian prairie agroecosytems. Soil Biology & Biochemistry 42:2192–2202.
- 14. Guo LJ, Zhang ZS, Wang DD, Li CF, Cao CG (2015) Effects of short-term conservation management practices on soil organic carbon fractions and microbial community composition under a rice-wheat rotation system. Biology and Fertility of Soils 51:65–75.
- 15. Six J, Bossuyt H, Degryze S, Denef K (2004) A history of research on the link between (micro) aggregates, soil biota, and soil organic matter dynamics. Soil & Tillage Research 79:7–31.
- 16. Lavelle P, Bignell D, Austen MC, Brown VK, Behan-Pelletier V, Garey JR, et al. (2004) Vulnerability of ecosystem services at different scales: role of biodiversity and implications for management. In: Wall DH (Ed.), Sustaining Biodiversity and Functioning in Soils and Sediments. Island Press, New York.
- 17. Wall DH, Bardgett R, Behan-Pelletier V, Herrick JE, Jones H, Ritz K, et al. (2012) Soil Ecology and Ecosystem Services. Oxford University Press, UK.
- 18. Ettema CH, Wardle DA (2002) Spatial soil ecology. Trends in Ecology & Evolution 17:177–183.
- 19. Dong HY, Kong CH, Wang P, Huang QL (2014) Temporal variation of soil friedelin and microbial community under different land uses in a long-term agroecosystem. Soil Biology & Biochemistry 69:275–281.
- 20. Giller KE, Beare MH, Lavelle P, Izac AMN, Swift MJ (1997) Agricultural intensification, soil biodiversity and agroecosystem function. Applied Soil Ecology 6:3–16.
- 21. White DC, MacNaughton SJ (1997) Chemical and molecular approaches for rapid assessment of the biological status of soils. In: Pankhurst CE, Doube BM, Gupta VVSR (Eds.), Biological Indicators of Soil Health. CAB, Wallingford, pp:371–396.
- 22. Diosma G, Aulicino M, Chidichimo H, Balatti PA (2006) Effect of tillage and N fertilization on microbial physiological profile of soils cultivated with wheat. Soil & Tillage Research 91:236–243.
- 23. Nautiyal CS, Chauhan PS, Bhatia CR (2010) Changes in soil physico-chemical properties and microbial functional diversity due to 14 years of conversion of grassland to organic agriculture in semi-arid agroecosystem. Soil & Tillage Research 109:55–60.
- 24. Qi J, van Keulen Herman, Huib H (2010) Modeling biomass, nitrogen and water dynamics in rice–wheat rotations. Agricultural Systems 103:433–443.
- 25. Kumari M, Chakraborty D, Gathala MK, Pathak H, Dwivedi BS, Tomar RK, et al. (2011) Soil aggregation and associated organic carbon fractions as affected by tillage in a rice-wheat rotation in North India. Soil Biology & Biochemistry 75:560–567.
- 26. Editorial Board of China Agriculture Yearbook (2012) China Agriculture Yearbook 2009, Electronic Edition. China Agriculture Press, Beijing, China.
- 27. Gartzia-Bengoetxea N, González-Arias A, Merino A, Martínez de Arano I (2009) Soil organic matter in soil physical fractions in adjacent semi-natural and cultivated stands in temperate Atlantic forests. Soil Biology & Biochemistry 41:1674–1683.
- 28. Vance ED, Brookes PC, Jenkinson DS (1987) An extraction method for measuring soil microbial biomass-C. Soil Biology & Biochemistry 19:703–707.
- 29. Jones JJB (2001) Laboratory guide for conducting soil tests and plant analysis. CTC, Boca Raton London, pp:140–142.
- 30. Jiang PK, Xu QF, Xu ZH, Cao ZH (2006) Seasonal changes in soil labile organic pools within a Phyllostachys praecox stand under high rate fertilization and winter mulch in subtropical China. Forest Ecology and Management 236:30–36.
- 31. Garland JL (1996) Patterns of potential C source utilization by rhizosphere communities. Soil Biology & Biochemistry 28:223–230.
- 32. Pengthamkeerati P, Motavalli P, Kremer R (2011) Soil microbial activity and functional diversity changed by compaction, poultry litter and cropping in a claypan soil. Applied Soil Ecology 48:71–80.
- 33. Grace JB, Anderson TM, Smith MD, Seabloom E, Andelman SJ (2007) Does species diversity limit productivity in natural grassland communities? Ecology Letters 10:680–689. pmid:17594423
- 34. Arbuckle JL (2006) Amos (Version 7.0) [Computer Program]. Chicago, SPSS.
- 35. Wang J, Wang X, Xu M, Feng G, Zhang W, Lu X (2015) Crop yield and soil organic matter after long-term straw return to soil in China. Nutrient Cycling in Agrocosystems 102:371–381.
- 36. Du Z, Ren T, Hu C (2010) Tillage and residue removal effects on soil carbon and nitrogen storage in the North China Plain. Soil Science Society of America Journal 74:196–202
- 37. Dikgwatlhe SB, Chen ZD, Lal R, Zhang HL, Chen F (2014) Changes in soil organic carbon and nitrogen as affected by tillage and residue management under wheat–maize cropping system in the North China Plain. Soil & Tillage Research 144:110–118.
- 38. Triberti L, Nastri A, Giordani G, Comellini F, Baldoni G, Toderi G (2008) Can mineral and organic fertilization help sequestrate carbon dioxide in cropland? European Journal of Agronomy 29:13–20.
- 39. Alvarez CR, Taboada MA, Gutierrez Boem FH, Bono A, Fernandez PL, et al. (2009) Topsoil properties as affected by tillage systems in the rolling Pampa region of Argentina. Soil Science Society of America Journal 73:1242–1250.
- 40. Zhang ZS, Guo LJ, Liu TQ, Li CF, Cao CG (2015) Effects of tillage practices and straw returning methods on greenhouse gas emissions and net ecosystem economic budget in rice-wheat cropping systems in central China. Atmospheric Environment 122:636–644.
- 41. Li CF, Zhou DN, Kou ZK, Zhang ZS, Wang JP, Cai ML, et al. (2012) Effects of tillage and nitrogen fertilizers on CH4 and CO2 emissions and soil organic carbon in paddy fields of central China. Plos One 7(5):e34642. pmid:22574109
- 42. Chivenge P, Vanlauwe B, Gentile R, Six J (2011) Comparison of organic versus mineral resource effects on short-term aggregate carbon and nitrogen dynamics in a sandy soil versus a fine textured soil. Agriculture, Ecosystems & Environment 140:361–371.
- 43. Hurisso TT, Davis JG, Brummer JE, Stromberger ME, Mikha MM, Haddix ML, et al. (2013) Rapid changes in microbial biomass and aggregate size distribution in response to changes in organic matter management in grass pasture. Geoderma 193–194:68–75.
- 44. Madejon E, Murillo JM, Moreno F, Lopez MV, Arrue JL, Alvaro-Fuentes J, et al. (2009) Effect of long-term conservation tillage on soil biochemical properties in Mediterranean Spanish areas. Soil & Tillage Research 105:55–62.
- 45. Golchin A, Oades JM, Skjemstad JO, Clarke P (1994) Study of free and occluded particulate organic matter in soils by solid state 13C P/MAS NMR spectroscopy and scanning electron microscopy. Australian Journal of Soil Research 32:285–309.
- 46. Zhao H, Lv YZ, Wang XK, Zhang HL, Yang XM (2012) Tillage impacts on the fractions and compositions of soil organic carbon. Geoderma 189–190:397–403.
- 47. Six J, Paustian K, Elliott ET, Combrick C (2000) Soil structure and organic matter. I. Distribution of aggregate-size classes and aggregate-associated carbon. Soil Science Society of America Journal 64:681–689.
- 48. Jiang YJ, Sun B, Jin C, Wang F (2013) Soil aggregate stratification of nematodes and microbial communities affects the metabolic quotient in an acid soil. Soil Biology & Biochemistry 60:1–9.
- 49. Nannipieri P, Ascher J, Ceccherini MT, Landi L, Pietramellara G, Renella G (2003) Microbial diversity and soil functions. European Journal of Soil Science 54:655–670.
- 50. Bending GD, Turner MK, Jones JE (2002) Interaction between crop residue and soil organic matter quality and the functional diversity of soil microbial communities. Soil Biology & Biochemistry 34:1073–1082.
- 51. Garbeva P, van Veen JA, van Elsas JD (2004) Microbial diversity in soil: selection of microbial populations by plant and soil type and implications for disease suppressiveness. Annual Review of Phytopathology 42:243–270. pmid:15283667
- 52. Baker JM, Ochsner TE, Venterea RT, Griffis TJ (2007) Tillage and carbon sequestration- what do we really know? Agriculture, Ecosystems & Environment 118:1–5.
- 53. Puget P, Chenu C, Balesdent J (2000) Dynamics of soil organic matter associated with particle-size fractions of water-stable aggregates. European Journal of Soil Science 51:595–605.
- 54. Colonego JC, Rosolem CA (2010) Soybean root growth and yield in rotation with cover crops under chiseling and no-till. European Journal of Agronomy 33:242–249.
- 55. Nunes MR, Pauletto EA, Denardin JE, Faganello A, Pinto LFS, Scheunemann T (2014) Persistence of chiseling effects on the compaction of a Nitisol under no-till in a humid subtropical region. Pesquisa Argopecuaria Brasileira 49:531–539.
- 56. Zak JC, Willig MR, Moorhead DL, Wildman HG (1994) Functional diversity of microbial communities: a quantitative approach. Soil Biology & Biochemistry 26:101–108.
- 57. Wang JJ, Zhang HW, Li XY, Su ZC, Xu MK (2014) Effects of tillage and residue incorporation on composition and abundance of microbial communities of a fluvo-aquic soil. European Journal of Soil Biology 65:70–78.
- 58. Lupwayi NZ, Arshad MA, Rice WA, Clayton GW (2001) Bacterial diversity in water stable aggregates of soils under conventional and zero tillage management. Applied Soil Ecology 16:251–261.
- 59. Chiu CY, Chen TH, Imberger K, Tian G (2006) Particle size fractionation of fungal and bacterial biomass in subalpine grassland and forest soils. Geoderma 130:265–271.
- 60. Simth AP, Marín-Spiotta E, Graaff MAD, Balser TC (2014) Microbial community structure varies across soil organic matter aggregate pools during tropical land cover change. Soil Biology & Biochemistry 77:293–303.
- 61. Stewart C, Plante A, Paustian K, Conant R, Six J (2008) Soil Carbon Saturation: Linking concept and measurable carbon pools. Soil Science Society of America Journal 72:379–392
- 62. Young IM, Crawford JW, Nunan N, Otten W, Spiers A (2008) Microbial distribution in soils: physics and scaling. Advances in Agronomy 100:81–121.
- 63. Carter MR (1996) Analysis of soil organic matter storage in agroecosystems. In: Carter MR, Stewart BA (Eds.), Structure and Organic Matter Storage in Agricultural Soils. CRC/Lewis Publishers, Boca Raton, FL, pp:3–11.
- 64. Choudhury SG, Srivastava S, Singh R, Chaudhari SK, Sharma DK, Singh SK, et al. (2014) Tillage and residue management effects on soil aggregation, organic carbon dynamics and yield attribute in rice–wheat cropping system under reclaimed sodic soil. Soil & Tillage Research 136:76–83.
- 65. Jha P, Garg N, Lakaria BL, Biswas AK, Rao AS (2012) Soil and residue carbon mineralization as affected by soil aggregate size. Soil & Tillage Research 121:57–62.
- 66. Miltner A, Bomback P, Schmidt-Brucken B, Kastner M (2012) SOM genesis: microbial biomass as a significant source. Biogeochemistry 111:41–55
- 67. Lenka NK, Lal R (2013) Soil aggregation and greenhouse gas flux after 15 years of wheat straw and fertilizer management in a no-till system. Soil & Tillage Research 126:78–89.
- 68. Dorodnikov M, Blagodatskaya E, Blagodatsky S, Marhan S, Fangmeier A, Kuzyakov Y (2009) Stimulation of microbial extracellular enzyme activities by elevated CO2 depends on aggregate size. Global Change Biology 15:1603–1614.
- 69. Denef K, Six J, Bossuyt H, Frey SD, Elliott ET, Merckx R, et al. (2001) Influence of dry-wet cycles on the interrelationship between aggregate, particulate organic matter, and microbial community dynamics. Soil Biology & Biochemistry 33:1599–1611.
- 70. Schutter ME, Dick RP (2002) Microbial community profiles and activities among aggregates of winter fallow and cover-cropped soil. Soil Science Society of America Journal 66:142–153.
- 71. Zhang PJ, Zheng JF, Pan GX, Zhang XH, Li LQ, Tippkötter R (2007) Changes in microbial community structure and function within particle size fractions of a paddy soil under different long-term fertilization treatments from the Tai Lake region, China. Colloids and Surfaces B: Biointerfaces 58:264–270. pmid:17507207
- 72. Santos NZ, Dieckow J, Bayer C, Molin R, Favaretto N, Pauletti V, et al. (2011) Forages, cover crops and related shoot and root additions in no-till rotations to C sequestration in a subtropical Ferralsol. Soil & Tillage Research 111:208–218.
- 73. Uren NC (2007) Type, amounts, and possible functions of compounds released into the rhizosphere by soil-grown plants. In: Pinton R, Varanini Z, Nannipieri P (Eds.), The Rhizosphere: Biochemistry and Organic Substances at the Soil–Plant Interface. CRC Press, Boca Raton, FL.
- 74. Minoshima H, Jackson LE, Cavagnaro TR, Ferris SSM, Temple SR, Mitchell JP (2007) Soil food webs and carbon dynamics in response to conservation tillage in California. Soil Science Society of America Journal 71:952–963.