- Open Access
Soil erosion affects variations of soil organic carbon and soil respiration along a slope in Northeast China
Ecological Processesvolume 8, Article number: 28 (2019)
Although soil erosion plays a key role in the carbon cycle, a holistic and mechanistic understanding of the soil erosion process within the cycle is still lacking. The aim of this study was therefore to improve our mechanistic understanding of soil organic carbon (SOC) and soil respiration dynamics through an experiment conducted in an eroding black soil farmland landscape in Northeast China.
The depositional profiles store 5.9 times more SOC than the eroding profiles and 3.3 times more SOC than the non-eroding profiles. A linear correlation between the SOC and 137Cs (Caesium-137) was observed in our study, suggesting that the SOC decreased with increased soil erosion. Furthermore, the fractions of intermediate C and the microaggregate C were lowest at the eroding position and highest at the depositional position. In the depositional topsoil, the input of labile materials plays a promotional role in soil respiration. Conversely, in the subsoil (i.e., below 10 cm), the potential mineralization rates were lowest at the depositional position—due to effective stabilization by physical protection within soil microaggregates. The field results of soil surface respiration also suggest that the depositional topsoil SOC is prone to be mineralized and that SOC at this depositional context is stabilized at subsoil depth. In addition, the high water contents at the depositional position can limit the decomposition rates and stabilize the SOC at the same time.
The findings from this study support that a majority of the SOC at footslope is stored within most of the soil profile (i.e., below 10 cm) and submitted to long-term stabilization, and meanwhile support that the depositional profile emits more CO2 than the summit due to its high amount and quality of SOC.
As the largest terrestrial carbon pool, the soil carbon pool is approximately 3.3 times the size of the atmospheric pool and 4.5 times the size of the biotic pool (Lal 2004a). Soil erosion and the subsequent transport of sediments by rivers represent a key pathway for soil carbon lateral transfer at the land surface, which has a profound effect on the carbon budget of terrestrial ecosystems (Ludwig et al. 1996; Li et al. 2018; Wang et al. 2019). However, propositions that soil erosion induces a carbon source or sink have been highly debated (Lal and Pimentel 2008). Previous studies have generally concluded that soil erosion leads to a terrestrial carbon loss due to the breakdown of structural aggregates and lower productivity in the eroding areas resulting from decreased soil nutrient (Jacinthe et al. 2002; Lal 2004b). In contrast, other studies from the last two decades have shown that soil erosion can induce a terrestrial carbon sink, due to the transfer and burial of high soil organic carbon (SOC) from eroded soil surface areas to depositional landform positions (Stallard 1998; Van Oost et al. 2007). The differences in understanding of the role of soil erosion in the carbon cycle reflect the uncertainties in quantifying a vertical flux controlled by interacting processes at large spatial and temporal scales. To better assess the erosion-induced terrestrial carbon sink or source at large scales, mechanisms involved in impacting carbon storage and flux need to be explored in detail at the landscape scale.
Within the landscape scale, soil lateral redistribution processes induced by water and tillage erosion can often affect carbon cycle dynamics. Initially, soil erosion may reduce plant production as a result of soil degradation and may decrease soil nutrient levels due to decomposition at eroding sites (Stallard 1998; Harden et al. 1999). Furthermore, initial deep burials of SOC can inhibit decomposition at deposition sites (Smith and Buddemeier 2005; Yoo et al. 2005). Moreover, the chemical or physical breakdown of soil can increase the decomposition of SOC during the detachment and transport processes (Lal 2003). In recent years, some models combining geomorphic factors with carbon dynamics have provided strong support for the assertion that lateral fluxes exert an important control on carbon vertical exchange at the landscape scale (Liu et al. 2003; Van Oost et al. 2005; Rosenbloom et al. 2006). Previous experimental studies have been conducted to investigate the observational mechanisms in eroding agricultural landscapes (Doetterl et al. 2012; Wiaux et al. 2014a; Wiaux et al. 2014b) or under natural vegetation conditions (Berhe et al. 2008; Berhe et al. 2012; Nadeu et al. 2012). However, a full mechanistic understanding of the effect of soil erosion and burial processes on vertical carbon dynamics (such as soil respiration, aboveground respiration, plant production, etc.) is still lacking (Kuhn et al. 2012). Specifically, the impacts of soil erosion on soil respiration (Rs), which is one of the most important ecological processes within our ecosystem, is still unclear.
Soil respiration is the largest vertical carbon efflux from soil to atmosphere and has the considerable potential to induce atmospheric carbon dioxide concentration variation—an increasingly alarming issue in context of global climate change (Yu et al. 2017). Soil respiration can indicate soil mineralization through SOC decomposition via microbes and can be affected by numerous factors including, but not excluding, soil temperature, soil moisture, and physical protection within soil aggregates (Doetterl et al. 2016). Thus, understanding mechanisms involved in soil respiration efflux is essential and has great research value for quantifying an erosion-induced vertical carbon flux.
Northeast China is a primary and important food production area in China, owing to its fertile soil which has a high organic matter content. However, after approximately 100 years of intense cultivation, the soil has been severely damaged by soil erosion (Zhang et al. 2007). Severe soil erosion has occurred since large-scale land reclamation began in the 1950s, and the thickness of black soils has decreased from 60 to 70 cm in the 1950s to 20–30 cm at present (Fang et al. 2012), exposing the loess parent material in some areas. Overall, approximately 4470 km2 of land in Northeast China has been subject to moderate to severe soil erosion, accounting for 38% of the total black soil acreage (Fang et al. 2006). Presently, there are few observational studies in Northeast China that explore the effects of soil erosion on SOC distribution and soil surface respiration fluxes at the landscape scale. However, the severe soil erosion in Northeast China highlights an urgent need to investigate the impacts of soil erosion processes on the carbon cycle.
The goal of this study was to conduct an experiment to improve our mechanistic understanding of SOC redistribution dynamics in an eroding black soil farmland landscape. We mainly focus on the SOC stocks and soil respiration dynamics in this study. Thus, our study was conducted as follows: First, we measured soil surface respiration fluxes along the cultivated slope, calculated the horizontal and vertical distribution of the SOC stocks, and quantitatively estimated the soil redistribution rate using 137Cs measurements. Second, we assessed the differences in the SOC pool composition and potential soil respiration along a geomorphic gradient through soil organic matter fractionation and incubation experiments. Third, we analyzed all results and assessed connections among them. In this paper, potential soil respiration represents soil respiration in optimal conditions for microbial activity and SOC decomposition—without the impacts of the varied soil water and temperature conditions.
Materials and methods
The study site is located at the Heshan Farm (125° 20′ 10.5″ E, 49° 00′ 23.1″ N) in Nenjiang County, Heilongjiang Province, Northeast China. The elevation of the area is 320 to 370 m above sea level. The slopes of cultivated land in this region range from 0.4 to 8.4%—with an average value of 4.2%. The climate is a semi-humid continental climate with a long cold winter, where the lowest and highest temperatures are − 20 °C in January and 21 °C in July, respectively (Zhang et al. 2007). The annual precipitation ranges from 300 to 750 mm, with an average of 534 mm and more than 90% of the precipitation falls between May and September (Liu et al. 2013). The primary soil type in this area is black soil, according to the Chinese genetic classification. The main textural classes of the topsoil are silt clay loam to clay loam, according to the USDA classification, with a sand content of 8–27%, a silt content of 29–66%, and a clay content of 26–40% (Wu et al. 2008). The study site was originally covered by natural forests and pastures and began to be converted into cultivated lands, particularly on the gentlest slopes, due to the needs of a dramatically increasing population and expropriation by ranches in the 1950s (Liu et al. 2015). In specific regard to the study site, soybean is the major crop, in rotation with wheat and corn.
We collected soil cores at four topographic positions (summit A1, convex shoulder A2, backslope A3 and footslope A4) along a hillslope (Fig. 1) at the study site before sowing in May 2015, and sampling was repeated three times at each location. Soil profiles were excavated down to the parent materials at each position. Soil samples were collected at 10-cm intervals for the top 30 cm soil depth and at 20-cm intervals for soils below 30 cm deep. In this study, the depth of fertile black soil at convex A2 and backslope A3 is approximately 30 cm due to serious soil erosion. In addition, our sampling was only one transect along the hillslope, leading to the lack of replicates at slope level. That is due to the limited width of the hillslope and other inoperable factors such as ground holes, etc.
Soil bulk density, carbon content, and 137Cs concentration were measured for each soil layer. The soil bulk density was measured using the oven-dried weight (drying at 105 °C for 24 h). SOC contents were measured using an elemental analyzer (vario EL III, Elementar, Hanau, Germany) as the black soils (pH < 7) were carbonate free, whereas 137Cs was measured using HPGe co-axial detectors coupled to a multi-channel analyzer. To minimize the uncertainties associated with the precision of the 137Cs measurements, 137Cs was detected at 662 keV using counting times at approximately 30,000 s. This method provides results with a counting error of less than 10% at the 95% confidence level. Concentrations were then converted into inventories per unit area using the soil depth and bulk density values. Estimates of soil loss and gain rates (t ha−1 year−1) can be derived from the 137Cs measurements by comparing the inventories measured at a specific point with the reference inventory. The reference 137Cs inventory of 2506 Bq m−2 is regarded as reliable in the study region (Fang et al. 2012). For an eroding site where the total 137Cs inventory is less than the reference inventory, soil erosion rates can be estimated using the simplified mass balance model proposed by Zhang et al. (1990). For the depositional position, the deposition rates were estimated using the proportional model proposed by Lowrance et al. (1988). The soil redistribution rates include the soil erosion rates at the eroding positions and the soil deposition rates at the depositional positions.
Soil temperature, soil moisture, and soil respiration measurements were conducted once a month during the growing season (May, June, July, and September) in 2015. We conducted field measurements at four topographic positions (Fig. 1) along the slope at the same time of each sample collection day. Soil temperature was measured with a portable digital thermometer. The volumetric moisture was measured using time-domain reflectometry (TDR300, Spectrum Technologies, USA). To better assess the soil respiration process and the SOC dynamics, samples (L1: 0–10, L2: 10–20, L3: 20–30, L4: 30–50, L5: 50–70, and L6: 70–90 cm) from these four slope positions (Fig. 1) were employed for the incubation experiments—soil respiration was measured using a Li-6400XT-09 Soil CO2 Flux Chamber (LI-COR, USA). The respiration of 50-g soil was monitored during a period of 182 days while keeping moisture (at 55% of the soil water-holding capacity) and temperature (20 °C) constant in an Erlenmeyer flask. The headspace air was sampled eight times during the incubation period using a gas-tight syringe. Before gas sampling, the headspace air in the flasks was thoroughly flushed with ambient air for 15 min. The flask was then capped immediately by sealing it with a rubber stopper for 3 h. The flasks were flushed with ambient air again after sampling and maintained with sealing membrane and the CO2 emission was detected by a gas chromatograph (Agilent 7890A, USA). In our analysis, we only considered the average respiration rates when heterotrophic soil respiration had stabilized.
We also conducted SOC fractionation experiments for the soil layers (L1: 0–10, L3: 20–30, and L5: 50–70, and for the depositional position, L6: 70–90 cm was added) at these four topographic positions (Fig. 1) to isolate the functional SOC fractions. We used the modified scheme described by Doetterl et al. (2012), which was based on the method proposed by Six et al. (1998), as a means of collecting and analyzing data. Through a series of physical and chemical fractionation techniques, we identified different particle sizes of SOC, i.e., water-stable macroaggregate C (> 250 μm), microaggregate C (250–53 μm), silt C (53–2 μm), and clay C (< 2 μm). Furthermore, three functional SOC pools (fast, intermediate, and passive), that differentiate in terms of stabilization mechanisms, were quantitatively estimated according to the method described by Doetterl et al. (2012).
Statistical tests for differences between the means of the geomorphic classes have been performed for the whole dataset, with tests for top and subsoil samples conducted separately using Bonferroni corrections and Tamhane’s T2 with SAS Enterprise 4.2 (SAS Institute Inc., Cary, NC, USA). Data for all four locations where aggregated together and linear regressions where performed to link SOC quality and respiration data to soil depth and quantitative estimates of soil redistribution rates.
Spatial patterns of soil moisture, temperature, and bulk density
During the growing season, the average soil moisture content varied at different slope positions. Along the topographical gradient, the soil moisture content generally declined with increasing altitude, except in the backslope A3 position. The lowest moisture was observed at backslope A3 and the highest moisture at footslope A4 (not shown). We found no evidence for systematic spatial differences in the temperature and the bulk density along the hillslope (not shown).
Soil erosion and soil organic content patterns
Based on the 137Cs measurements, we quantitatively estimated that the soil erosion rates for A1, A2, and A3 were − 3.5 t ha−1 year−1, − 47.2 t ha−1 year−1, and − 56.1 t ha−1 year−1, respectively, and the soil deposition rate for A4 was approximately 56.9 t ha−1 year−1. Thus, we grouped the soil profiles taken along the geomorphic gradient into three classes according to their geomorphic settings: (i) the non- (or slowly) eroding profile at summit position A1, (ii) the eroding profiles on convex shoulder A2 and backslope A3, and (iii) the depositional profile at the footslope position A4. The vertical distribution of the SOC concentrations and inventories at various landscape positions are shown in Fig. 2. The topsoil SOC contents ranged from 8.1 to 24.4 g/kg at the four positions. At the eroding positions and the non-eroding position, the SOC concentrations varied by locations and decreased with increasing soil depth. The SOC concentrations were higher for the depositional and the non-eroding profiles than for the eroding profiles. The soils of the depositional profiles were enriched in SOC at subsoil depth and the SOC contents at the footslope position first increased and then decreased with the soil depth (Fig. 2a). The depositional profiles store 5.9 times more SOC than the eroding profiles and 3.3 times more SOC than the non-eroding profiles (Fig. 2b). The SOC and the 137Cs were positively correlated in our study area, as were the SOC and the soil redistribution rates (Table 1).
Spatial distribution of soil respiration
We found consistent patterns of soil surface respiration fluxes in May, June, July, and September 2015 (Fig. 3a). The respiration rates were highest at the depositional position and lowest at the eroding position. This pattern coincided with the variations in the SOC stocks along the hillslope. When averaged over the period of observation, the ratios of soil respiration (μmol m−2 s−1) to the SOC inventory (kg m−2) were compared along the slope. The eroding profiles had a slightly higher Rs/SOC (μmol kg−1 s−1) than the non-eroding profiles. The Rs/SOC was lowest at the depositional position for both the 0–30 cm and the 0–90 cm layers (Fig. 3b).
In the incubation experiments, the respiration rates of the topsoil samples (0–10 cm) were higher than those of the subsurface soils (10–90 cm) (Fig. 4). The measured respiration rate was negatively correlated with depth, whereas positive correlations with the SOC concentration can be identified (Table 1). The soil respiration per unit soil (g) for the topsoil samples was the lowest at the eroding profiles, while the depositional profiles respired at significantly higher rates (Fig. 4a). For subsurface soils, the highest respiration rates were found for the depositional profiles, and this respiration was significantly higher than the respiration of the non-eroding and eroding profiles (p < 0.1) (Fig. 4a).
The topsoil samples also respired at a higher rate than the subsoils per unit SOC (g). For the 0–10 cm layer, the potential respiration rates were higher at the depositional position than at the non-eroding position (Fig. 4b). For the subsoil (10–90 cm), the lowest respiration rates were measured in the depositional profiles and were significantly lower than the respiration rates of the non-eroding profiles (p < 0.1) (Fig. 4b). Samples from the eroding profiles respired at a higher rate than those from the depositional or non-eroding profiles (Fig. 4b).
Spatial patterns of the SOC fractions and pools
We observed a significant positive correlation between the soil depth and the proportion of the passive pool C (p < 0.01) and a negative correlation between the soil depth and the fast pool (Table 1). The depositional profiles contained a slightly greater proportion of the SOC in the fast pool relative to the non-eroding or eroding profiles (Fig. 5a). More SOC is associated with the intermediate pool in the depositional profiles than in the non-eroding or eroding profiles (Fig. 5a). We found a significant positive correlation (p < 0.05) between the soil redistribution rates and the fractions of C in the intermediate pool (Table 1, Fig. 6b) and in microaggregates (Table 1). Proportionally more SOC was stored in the intermediate pool and in the microaggregates at the depositional position. This intermediate pool can mainly reflect the contribution of the microaggregate C in our study. We also observed a significant negative correlation (p < 0.05) between the intermediate pool (or the microaggregate C) and the subsoil potential respiration per unit SOC (Table 1).
Effects of soil redistribution on the SOC
Our study showed that the depositional profiles were enriched in SOC at subsoil depth and that they stored significantly more SOC than the non-eroding or eroding profiles (Fig. 2), which is consistent with many previous studies (Berhe et al. 2008; Doetterl et al. 2012; Wang et al. 2013; Wiaux et al. 2014a). A previous study showed that SOC depletion took place at eroding sites and SOC accumulation took place at depositional sites (Dlugoß et al. 2012). Being a selective process, soil erosion preferentially transfers fine and light materials, which are typically enriched in SOC relative to the bulk soil (Wairiu and Lal 2003). This process can lead to carbon loss in the eroding profiles and enrichment of the labile C fraction in the depositional profiles. For example, Wiaux et al. (2014a) observed a spatial differentiation of the labile SOC pool (i.e., the SOC not resistant to NaOCl), with a significant enrichment for the 0–1 m layer in the depositional profiles along a hillslope in the Belgian agricultural loam belt. In our study, we also observed a greater proportion of SOC in the fast pool at the depositional position (Fig. 5a), which can confirm the processes preliminarily. The SOC concentrations and the fractions of fast C and intermediate C were higher at the depositional position; thus, it should be discussed separately on whether the lower respiration rates per unit SOC benefited from the effective physical protection there.
Controls on potential soil respiration
We conducted incubation experiments to quantify the potential soil respiration without the impacts of the varied soil water and temperature conditions. Soil incubation studies are advantageous for assessing the SOC decomposition rates of different C fractions, as there is usually no new input of organic material during the course of an incubation study and the fast C pool is depleted without being replaced (Schädel et al. 2013). Soil incubation studies lasting longer than 100 days can reduce the dominance of the fast C pool and will show the contributions of the more recalcitrant pools in context of soil CO2 emissions (Von Lützow and Kögelknabner 2009). Thus, our long-term incubation experiment can better reflect the potential respiration for the fast, intermediate, and passive pools during the 182 days.
In recent years, newly emerging evidence has indicated that molecular structure and/or chemical composition do not solely predetermine the persistence of SOC and that instead environmental factors can exert an additional influence upon SOC mineralization (Han et al. 2016). In both eroding and depositional landscapes, the C in soil can be stabilized against decomposition by two major mechanisms: (a) chemical association of the SOC with mineral surfaces and (b) physical protection of the SOC, either by spatial separation from decomposers or by inaccessibility due to the encapsulation of SOC within soil aggregates (Doetterl et al. 2016).
This study also focuses on the analysis of inner physical protection mechanisms. Soil erosion slackens and breaks down water stable aggregates, thus leading to encapsulated C being prone to mineralization (Lal 2003). According to the method in this study, the intermediate pool can mainly reflect the contribution of the microaggregate C. Our result showed that the fractions of the intermediate C and the microaggregate C were lowest at the eroding position and highest at the depositional position (Table 1, Fig. 6), providing a reasonable explanation for the observed highest potential soil respiration at the eroding position. In the uppermost topsoil (0–10 cm), the SOC mineralization rates were higher at the depositional position than at the non-eroding position, reflecting the input of the labile organic matter fractions. Conversely, in the subsoil, the mineralization rates were lowest at the depositional site (Fig. 4), because of effective stabilization by physical protection within soil microaggregates. These findings indicate that physical protection mechanisms play a dominant role in the subsoil (i.e., below 10 cm) in stabilizing SOC against decomposition. In the depositional topsoil, the input of labile materials plays a major role in soil respiration.
Controls on soil surface respiration fluxes
Soil surface respiration fluxes can be used as an indicator of the persistence of SOC (Wiaux et al. 2014b). The temporal variability in Rs at a single point can be reasonably described by changes in soil temperature and moisture, while the spatial variability is much more difficult to determine. Relatively inconsistent views about the effect of soil redistribution on the spatial variability of CO2 effluxes exist. Some studies reported higher respiration rates at footslope positions relative to summit and shoulder positions (Reicosky et al. 2005; Webster et al. 2008; Wiaux et al. 2015), but opposite trends were also observed in some regions (Epron et al. 2006; Wei et al. 2014; Zhang et al. 2016).
In our study, the respiration rates were highest at the depositional position, while the Rs/SOC was lowest at that position (Fig. 3). These results support that the SOC at such a footslope is stored along the soil profile and involved in a long-term stabilization process and simultaneously support that the depositional profile emits more CO2 than the summit due to its high amount and quality of SOC. Wiaux et al. (2015) reported that in crop soils, approximately 90 to 95% of the fluxes originated from the first 10 cm of the soil profile at the footslope, while at the summit, the first 30 cm of the soil profile significantly contributed to surface fluxes. These results suggest that the depositional topsoil SOC is prone to be mineralized, and the SOC in this depositional context is stabilized at subsoil depth.
The analysis of the results of the field experiments are in agreement with those of the incubation experiments preliminarily, suggesting that physical protection mechanisms are vital in the processes of SOC decomposition. In addition, a previous study showed that CO2 efflux was also regulated by a complex interplay of different environmental factors, such as soil moisture, soil temperature, and soil porosity (Van Hemelryck et al. 2011). In our study, the protective effects of soil deposition on soil respiration per unit SOC were more remarkable in field conditions than in indoor ones (Fig. 3b and Fig. 4b), most likely due to the impacts of the varied soil water conditions.
Soil moisture is identified as a major environmental driver regulating the spatial variability of soil respiration in many studies (Wei et al. 2014; Wiaux et al. 2014b; Zhang et al. 2016). In general, soil water contents are higher at lower altitudes because of gravity. Previous studies have suggested that excessive soil water can limit SOC decomposition by altering the aeration status and stressing soil microbial activity (Zhang et al. 2016). We observed high water contents at the depositional position, which can obstruct CO2 fluxes, and anaerobic conditions prevail, depressing the activity of aerobes, thus stabilizing SOC as a result.
This study investigated the impacts of soil erosion on the soil organic carbon and soil respiration in black-soil sloping farmland in Northeast China. The results show that the depositional profiles store 5.9 times more SOC than the eroding profiles and 3.3 times more SOC than the non-eroding profiles. The soils of the depositional profiles were enriched in SOC at subsoil depth, and the SOC contents at the footslope position first increased and then decreased with the soil depth. A linear correlation between the SOC and 137Cs was observed in our study, suggesting that the SOC decreased with increased soil erosion. In the depositional topsoil, the input of labile materials plays a promoting role in soil respiration. By contrast, in the subsoil (i.e., below 10 cm), the potential mineralization rates (per unit SOC) were lowest at the depositional position because of effective stabilization by physical protection within soil microaggregates. The field results of the soil surface respiration per unit SOC also suggest that the depositional topsoil SOC is prone to be mineralized and the SOC in this depositional context is stabilized at subsoil depth. These findings support that the SOC at such a footslope is primarily stored along most of the soil profile (i.e., below 10 cm) and is involved in long-term stabilization and meanwhile support that the depositional profile emits more CO2 than the summit due to its high amount and quality of SOC. Furthermore, the high water contents at the depositional position limit decomposition rates and stabilize SOC at the same time.
- CO2 :
Soil organic carbon
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This study was supported by the National Key Research and Development Program (2016YFA0602701), National Natural Science Foundation of China (31570468), Changjiang Young Scholars Programme of China (Q2016161), National Youth Top-Notch Talent Support Program, and Fok Ying Tung Education Foundation (151015). The experiments were supported by the Beijing Normal University Jiusan Soil and Water Conservation Station.
This study was supported by the National Key Research and Development Program (2016YFA0602701), National Natural Science Foundation of China (31570468), Changjiang Young Scholars Programme of China (Q2016161), National Youth Top-Notch Talent Support Program, and Fok Ying Tung Education Foundation (151015).
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