Soil organic carbon stabilization mechanisms and temperature sensitivity in old terraced soils
Being the most common human-created landforms, terrace construction has resulted in an extensive perturbation of the land surface. However, our mechanistic understanding of soil organic carbon (SOC) (de-)stabilization mechanisms and the persistence of SOC stored in terraced soils is far from complete. Here we explored the factors controlling SOC stability and the temperature sensitivity (Q10) of abandoned prehistoric agricultural terrace soils in NE England using soil fractionation and temperature-sensitive incubation combined with terrace soil burial-age measurements. Results showed that although buried terrace soils contained 1.7 times more unprotected SOC (i.e., coarse particulate organic carbon) than non-terraced soils at comparable soil depths, a significantly lower potential soil respiration was observed relative to a control (non-terraced) profile. This suggests that the burial of former topsoil due to terracing provided a mechanism for stabilizing SOC. Furthermore, we observed a shift in SOC fraction composition from particulate organic C towards mineral-protected C with increasing burial age. This clear shift to more processed recalcitrant SOC with soil burial age also contributes to SOC stability in terraced soils. Temperature sensitivity incubations revealed that the dominant controls on Q10 depend on the terrace soil burial age. At relatively younger ages of soil burial, the reduction in substrate availability due to SOC mineral protection with aging attenuates the intrinsic Q10 of SOC decomposition. However, as terrace soil becomes older, SOC stocks in deep buried horizons are characterized by a higher temperature sensitivity, potentially resulting from the poor SOC quality (i.e., soil C:N ratio). In conclusion, terracing in our study site has stabilized SOC as a result of soil burial during terrace construction. The depth–age patterns of Q10 and SOC fraction composition of terraced soils observed in our study site differ from those seen in non-terraced soils, and this has implications when assessing the effects of climate warming and terrace abandonment on the terrestrial C cycle.
Please read the corrigendum first before continuing.
Since post-Neolithic times, the construction of terraces has played an important role in the expansion and intensification of agriculture for food production (Brown et al., 2021). Terracing is recognized as a major adaptive strategy for land use in hilly areas and as an efficient conservation practice that provides multiple ecosystem services, e.g., erosion control and enhanced biomass yields, soil water recharge, and nutrient storage (Dunjó et al., 2003; Tarolli et al., 2014, 2015; Wei et al., 2016). At the same time the construction of terraces influences soil carbon dynamics by land-use change and the alteration of local topography and hydrological conditions (Shi et al., 2019; Stavi et al., 2019). Although the impact of terracing on soil organic carbon (SOC) stocks has been studied in diverse regions in Europe (Curtaz et al., 2015; Dunjó et al., 2003; Walter et al., 2003), Asia (Chen et al., 2020; Shi et al., 2019), South America (Antle et al., 2007), and Africa (Kagabo et al., 2013), the mechanisms responsible for the observed C gain and loss due to terracing are unclear. For example, both positive and negative effects of terracing on SOC stock have been reported (Gao et al., 2020; Chen et al., 2020; Brown et al., 2021). This knowledge gap limits our ability to evaluate how SOC stocks in terraced systems will respond to present and future environmental change such as terrace degradation or land-use change.
Terraces are developed through active cut or fill processes conducted along hillslopes or as a consequence of erosion, deposition, and cultivation (Mesfin, 2016). Soil redistribution during terrace development results in an exposure of the subsurface soil at the cut or eroding section, as well as burial of the original topsoil at the fill or deposition section. Thus, the impacts of terrace construction on SOC dynamics can be compared to the mechanisms proposed for erosional impacts given the similar soil redistribution patterns, that is, topsoil removal at erosional position (same as cut section) and soil burial at depositional position (fill section) (De Blécourt et al., 2014; Van Oost et al., 2007). Based on the knowledge from erosional studies, three possible mechanisms that link terracing with SOC stabilization, acting together or separately, should be considered: (i) the removal of topsoil and physical breakdown of soil aggregates during terrace construction enhance the decomposition of SOC (Bailey et al., 2019; Doetterl et al., 2016; Gao et al., 2020); (ii) SOC removal at the cut or eroding section is gradually replaced through continued SOC inputs from new photosynthate and plant litter decomposition (Berhe et al., 2007; Harden et al., 1999); and (iii) burial of the original topsoil at the fill or depositional section results in reduced SOC decomposition rates by changing the environmental context for SOC decomposition, e.g., providing a low-mineralization context by reducing oxygen availability in soil pore space and increasing soil water content (Berhe et al., 2007; Vandenbygaart et al., 2012; Wang et al., 2014; Wiaux et al., 2015). The status of SOC stocks of terraces but also to what extent terraced soil systems will represent a net SOC loss or sink largely depend on the magnitude by which the three mechanisms identified above interact and govern SOC dynamics over time.
Predicting the sensitivity of SOC decomposition to temperature change is vital to evaluate the warming-induced changes in soil SOC stock and its feedbacks to climate change (Kirschbaum, 1995; Knorr et al., 2005). However, the fundamental drivers and basic patterns of the temperature sensitivity of SOC decomposition in agricultural terraces have been poorly described so far. In a recent study the effect of terrace construction on soil CO2 emission and temperature sensitivity on the Chinese Loess Plateau was reported. However, the simulation of topsoil removal during terrace construction only reflected the short-term (< 2 years) response and mechanisms (Gao et al., 2020). On the basis of the fundamental principles of enzyme kinetics, temperature sensitivity of SOC decomposition (Q10) should be determined by the chemical complexity of SOC molecules and by the availability of the SOC substrate to decomposers (Davidson and Janssens, 2006). On the one hand, chemically more complex SOC molecules (thus SOC of low quality), that is, those that require a high activation energy to degrade, should have a higher Q10 than SOC of higher substrate quality (Bosatta and Ågren, 1999). On the other hand, environmental factors (e.g., SOC protection) as a constraint on substrate availability should have a negative effect on observed Q10 values (Gillabel et al., 2010). According to the fundamental principles mentioned above, the buried SOC stock at fill sections of a terrace is likely to be less sensitive to warming given the high quality of this C stock. However, the labile fraction of this buried SOC stock might be gradually decomposed or transferred into protected SOC fractions as the terrace system ages (Wang et al., 2014). This changes the SOC quality and protection (and hence substrate availability) over time. We hypothesize that the terrace age is a fundamental driver of the evolution of soil geochemical properties, which in turn determines the SOC protection and quality and thus SOC stabilization and temperature sensitivity. These time-dependent mechanisms may have important implications for the future status of terrace SOC and its feedbacks to climate change.
The overall objective of this study is to improve the mechanistic understanding of SOC dynamics in agricultural terraces and its potential feedback to climate change. To achieve this, we combined SOC fractionation experiments and temperature sensitivity incubations with measurements of relative terrace soil burial age on a prehistoric agricultural terrace system in the Ingram Valley of NE England. The detailed objectives of this study are to investigate (i) the factors controlling SOC stabilization in old agricultural terraces and (ii) the associated patterns of SOC temperature sensitivity.
2.1 Study sites
The study area is located in the Ingram Valley (Fig. 1a) in the Cheviot Hills of NE England within the Northumberland National Park (55∘26′26.14′′ N, 1∘59′49.52′′ W). This region is characterized by maritime temperate climate with an average monthly temperature that ranges between −1 ∘C (in February) and 18 ∘C (in July and August) and an average annual rainfall of around 650 mm (https://www.meteoblue.com, last access: 20 May 2020). Umbrisols have developed from Andesite igneous bedrock of the Cheviot Volcanic Formation which formed approximately 393 to 419 million years ago in the Devonian (British Geological Survey, 2018). The study site complex is one of the largest monuments in England (5.7 km2) and is known as a multi-period archeological landscape, as well as currently also being investigated as part of project TerrACE (https://www.terrace.no/, last access: 3 December 2021). Previous archeological investigations during 1997–1999 (Frodsham and Waddington, 2004) indicate that the cultivation terraces have a prehistoric origin and date back as far as the early Bronze Age, ca. 1800–1500 BC. The landscape at the time the terraces were built was likely dominated by dwarf shrubs (Ericaceae) and grasses, while during the Romano-British period cereals were identified in a pit feature cut into one of the terrace surfaces (Frodsham and Waddington, 2004). The study area is covered by terraces in a small area of ca. 9000 m2 (Fig. 1c).
2.2 Soil sampling
Topographic data in the sampling area were collected through structure-from-motion (SfM) photogrammetry technique integrating ground-based and UAV (nadir and oblique) images for a complete and detailed survey of the terrace system (Cucchiaro et al., 2020a). This technique allowed for the generation of high-resolution digital terrain models at 0.25–0.10 m resolution that helped identify the extent and shape of seven prehistoric agricultural terraces. Moreover, the output of the SfM workflows as point clouds allowed for the extraction of profiles and sections of the opened trench (Cucchiaro et al., 2020b). A detailed stretch map was created (Fig. 1c; Cockcroft and Waddington, unpublished technical report, 2020) for supporting data interpretation. In order to produce a continuous section through seven cultivation terraces, a trench measuring 63 m long by 1.5 m wide was excavated in May 2019 (Fig. 1b). The trench was then carefully cleaned to the depth of the weathered bedrock surface in order to expose the full nature and extent of any archeological features, structures, and deposits where they survive. Four terraces (P1, P2, P3, P4) were sampled in detail along the trench in order to cover the full range of potential burial ages present in the sequence (Fig. 1). Additionally, two control soil pits (C1, C2) were excavated in proximity to the terraces to provide an undisturbed soil profile, that is, a soil profile that was not subjected to terracing. Soil samples were collected every 5 cm except for P1 where a different depth interval was used for subsoil layers (Table 1). Thus, whilst our sampling approach only covers one field trench, our approach is a suitable compromise between the need for spatial representativeness of soil data and the logistical criteria for detailed geo-archeological excavations at selected sites. The number of highly depth-resolved samples collected this way does allow for the analysis of continuous trends of specific soil parameters within terraced and non-terraced profiles along a sequence of spatially and temporally clearly distinct agricultural terraces. A total of 91 depth-explicit soil samples have been collected this way along the terrace sequence and an additional 23 depth-explicit samples collected from the control pits for further analysis.
2.3 SOC fractionation
A total of 40 g of 5 mm sieved air-dried soils was fractionated in duplicate to obtain SOC fractions for selected soil layers, representing different layers within each undisturbed and terraced soil (topsoil 0–10 cm, shallow subsoil 30–45 cm, deeper subsoil ≥ 60–70 cm). These depth intervals were chosen to maximize the variation in terrace burial age, which we will use to investigate its effect on C dynamics. We used a fractionation scheme based on the conceptual SOC model proposed by Six et al. (2002, 1998) applying a simplified version of its fractionation protocol (Doetterl et al., 2015). Total SOC was fractionated into coarse particulate organic carbon (cPOM, > 250 µm), microaggregate-associated SOC (M, 250–53 µm), and non-aggregated silt and clay SOC (S + C, < 53 µm). In brief, the microaggregate isolator was placed on a reciprocal shaker, and 20 g of air-dried soils, together with 50 glass beads, was added on top of a sieve with a 250 µm mesh size. Then, the isolator and sieve were flushed continuously with deionized water while shaking at low (= 150 rpm) speed for up to 5 min until water flowing out of the device onto a 53 µm mesh size sieve was clear and all aggregates on top of the 250 µm mesh size sieve were broken up. Materials left on the 250 µm mesh size sieve were interpreted as cPOM plus sand. Materials left on the 53 µm mesh size sieve were interpreted as microaggregates, and all < 53 µm particles were interpreted as non-aggregated silt and clay. All fractions were analyzed for total C and N using a vario Max CN Analyzer (Elementar GmbH, Germany). Samples showed no reaction when treated with 10 % HCl and were considered free of carbonates. cPOM was interpreted as unprotected SOC, while M and S + C were interpreted as mineral-protected SOC in our analysis (Gillabel et al., 2010; Six et al., 2002).
2.4 Temperature-sensitivity based on soil incubations
Three replicate samples of 30 g of 2 mm sieved bulk soils from the selected soil layers were chosen for the fractionation (see Table 1) of each soil profile and were incubated at two different temperature levels (20 and 30 ∘C) using 380 mL sealed jars. A 10 d pre-incubation was carried out in order to avoid CO2 pulses caused by soil sample preparation (i.e., sieving, drying, and rewetting), then respiration was monitored during 8 weeks while keeping moisture (60 % of soil water holding capacity) constant during the whole experiment by periodically adding demineralized water to the samples. The temperature and moisture level used in the incubation were chosen to provide optimal conditions for microbe activity, thus inducing the specific potential maximum heterotrophic respiration (SPR) (Paul et al., 2001). Then, respiration data were collected to calculate heterotrophic potential specific soil respiration, expressed as CO2-C per unit mass of soil C. For this, every 7 d throughout the experiment gas samples within the incubation jars were circulated through a LI-830 CO2 gas analyzer (LI-COR, Inc., the Netherlands) for determining CO2 concentration. CO2 production was analyzed as the average SPR over the whole incubation period (pre-incubation excluded). To avoid CO2 saturation effects influencing microbial decomposition processes, the incubation jars were flushed with fresh air after each measurement and left open between measurement cycles with jars covered by parafilm to allow for gas exchange while limiting water loss through evaporation. Temperature sensitivity of SPR (Q10) was calculated as the difference in SPR of the same aliquot samples at 20 to 30 ∘C incubation temperature (Doetterl et al., 2018; Paul et al., 2001). The average uncertainty for SPR measurement was 0.5 .
2.5 Soil burial age and soil geochemical properties along the agricultural terraces
The main total elemental contents (Fe, Al, Mn, Sr, Rb) of the bulk soil were measured using an Olympus Vanta M series portable energy dispersive X-ray fluorescence spectrometer (pXRF) at each 5 cm depth for all terrace profiles (Table 1). The Rb:Sr ratio was applied as a proxy for weathering intensity since both elements fractionate during the weathering processes due to their different chemical behavior. Because of the relative inertness of Rb compared to Sr, a higher ratio of Rb:Sr indicates a higher degree of soil weathering and higher age (An et al., 2018). Soil pH was determined with a soil : solution ratio of 1:2.5 () with 0.01 M CaCl2 solution using a pH meter (Mettler Toledo MP220, Mettler Toledo, Switzerland). Soil texture was analyzed using a laser diffraction particle size analyzer (model LS 13 320; Beckman Coulter Inc., Fullerton, USA) after ultrasonic dispersion and removal of organic matter using H2O2 (35 %) (Beuselinck et al., 1998).
Optically stimulated luminescence (OSL) has been widely applied for sediment dating (Brown, et al., 2021). To establish a chronology of soil burial along the terrace sequence, OSL data were obtained using a portable OSL (pOSL) reader. A pOSL reader was used since it has successfully and frequently been applied in similar settings (e.g., Muñoz-Salinas et al., 2011; Portenga et al., 2016; Porat et al., 2019). When compared to conventional OSL dating, pOSL is more efficient in terms of time, cost, and labor and can therefore be used for large, untreated samples, especially to clarify deposition processes (Muñoz-Salinas et al., 2011; Porat et al., 2019). The pOSL was recorded at 5 cm intervals throughout all terrace profiles (P1–P4). Luminescence samples were collected in bulk using blackout bags to block out the light. The bags were held against the cleaned section at the sampling location, and soil was scooped into them, avoiding exposure to the light. Counts were based on 60 s of exposure to blue light using the SUERC (Scottish Universities Environmental Research Centre) meter. Here, besides others, the signal intensity is a function of mineral composition, content of moisture, age, etc. As mineral composition, as well as moisture content, was relatively homogenous throughout individual profiles, age is the main discriminant for pOSL activity. The consistently low photon counts at the top of the soil profiles were therefore taken as an indicator of very young ages. Thus, pOSL activity was taken as a proxy for the relative terrace soil burial age (following Muñoz-Salinas et al., 2011) in which it increased monotonically with soil depth. Note that the interpretation of relative terrace soil burial age based on pOSL was only applied with depth within individual soil profiles rather than between profiles to rule out batch effects caused by the drying out of the samples which could not be processed in the field. Where pOSL did not increase consistently with depth, it was considered to indicate soil heterogeneity and mixing. Lastly, soil samples were classified into relatively younger and older soils based on a (visual) change in the soil depth–age relation (see Fig. 2). Then, the relationship of SOC fraction abundance and Q10 to soil burial age was analyzed by comparing sample groups along the four investigated terraces. The pOSL signal showed that the terrace soil profiles gradually become older towards the bottom (Fig. 2), suggesting that the terraces are most likely developed by stone lines which gradually catch soil material moving downslope, resulting in the former “topsoil” layers being buried in deep soil layers. Therefore, the soil burial age was supposed to play a dominant role in terracing SOC dynamics.
2.6 Statistical analysis
All statistical analyses were performed by R 3.6.3 (R Development Core Team, https://www.r-project.org/, last access: 6 December 2021). The differences of SOC concentration between control and terraced soil layers were analyzed with unpaired t tests. The model fitting function of “stat_fit_glance” from the “ggpmisc” R package was used to derive the non-linear regression model between terrace soil burial age and SOC variables (Q10, SPR, SOC fractions). Linear regression and simple correlation were used to examine the relationship between SOC fractions, Q10, pH, and soil texture. Differences in means of SPR and Q10 between the buried and non-buried soil layers were tested by unpaired t tests. The “outlierTest” function from the “car” package was used to identify outliers (P < 0.05) based on a given model (i.e., cPOM % ∼ Q10; S + C % ∼ SPR; total photon counts ∼ log(Q10); total photon counts ∼ log (SPR)). The observation for the Q10 from P1 topsoil (see gray point in Fig. 5a) was identified as an outlier and was therefore not included in the correlation and regression analysis. Significance in all cases was assessed at P < 0.05. All figures were produced by R package “ggplot2”.
3.1 SOC fractions composition, temperature sensitivity, and soil respiration
For the 0–50 cm soil layers, no significant difference in SOC concentrations could be observed between the terrace and control soil layers (Fig. 3a). Below 50 cm, soil layers in control profiles showed significant lower SOC contents relative to the terrace soil layers (P < 0.05). The SOC contents (Fig. S1 in the Supplement) of P1 for 95–125 cm, P2 for 65–85 cm, P3 for 50–65 cm, and P4 for 55–70 cm depth layers were higher than at the control profiles (C). In combination with the high degree of chemical weathering, we interpreted these layers as buried A horizons (detailed in S1 in the Supplement).
Considering all profiles, topsoil SOC was mainly composed of SOC associated with the M fraction, followed by cPOM and S + C (Fig. 3b). For the 30–45 cm depth layer, terrace soil layers contained twice as much cPOM-associated C than the corresponding soil layer in the control profiles. Below 60 cm (i.e., the buried horizons), the contribution of cPOM to total SOC in terrace soil layers was 1.7 times higher than in soil layers of the control, while a comparable proportion of physical-protected SOC (M %) was found in terrace and control soil layers. SPR and SOC temperature sensitivity (Q10) varied significantly across soil layers. On average, buried soil layers showed a significantly lower SPR than the non-buried layers (P < 0.05, Fig. 4), while for Q10 no significant difference between buried and non-buried soil layers could be found.
3.2 Controls on terrace SOC stability
A non-linear regression analysis was used to identify the effect of total photon counts, which was treated as a proxy for soil burial age, on SOC fraction distributions and on SPR. We found that SPR was negatively related to total photon counts (Fig. 5a), indicating that the terrace soil burial age was an important control on SPR. Furthermore, cPOM and S + C fractions were significantly correlated with burial age (Fig. 5b), in which a shift from cPOM to S + C-associated SOC fractions was observed with increasing age. No significant relationship between SPR and measured soil geochemical properties (e.g., pH, soil texture, and soil elements) was found (Table 2, P < 0.05).
3.3 Terrace soil burial age and SOC temperature sensitivity (Q10)
A significant relationship between Q10 and total photon counts was observed (Fig. 5a). This relationship suggests that Q10 values decline rapidly with the increasing age for young soil horizons, while for older soil horizons Q10 remained relatively constant or increased in the oldest soil horizons. Linear regression further showed that for relatively younger soil horizons (Fig. 2), Q10 values were significantly related to the proportion of S + C-associated C and cPOM-associated C, while for old soil horizons no such strong relation was found (Fig. 6).
∗ P < 0.05. N=13. cPOM = coarse particulate C; M = microaggregate-associated C and S + C = silt- and clay-associated C.
To further identify the underlying controls, we linked the patterns of Q10 to soil C:N ratio and measured soil geochemical properties (e.g., pH, soil texture). We found that Q10 was significantly correlated to the C:N ratio of bulk soil, M, and S + C fractions (Table 3). In addition, Fig. 7 shows that the C:N ratio of bulk soil and SOC fractions first decreased with burial age then significantly increased (P < 0.05) when the terrace soils became very old. Furthermore, the Q10 was significantly correlated to clay content at relatively younger burial ages, while silt and sand contents were significantly correlated to Q10 at relatively older burial ages (Table 2, P < 0.05).
4.1 Terrace SOC stabilization: importance of carbon burial and terrace age
Previous work has highlighted that carbon burial due to soil redistribution has important implications for SOC stabilization in eroding landscapes (e.g., VandenBygaart et al., 2012; Van Oost et al., 2012; Wang et al., 2014, 2015). Our results show that the buried soil layers have a significantly lower SPR than the non-buried layers (Fig. 4), indicating that carbon burial by terracing reduces soil potential respiration and is therefore a mechanism that contributes to SOC stabilization in agricultural terraces. Although buried A horizons in terrace profiles contain 1.7 times more unprotected SOC (cPOM, Fig. 4) than non-terraced profiles, the less favorable environmental conditions for microbial decomposers (e.g., mostly lack of oxygen and water saturation) are likely to constrain in situ mineralization rates of SOC (De Blécourt et al., 2014; Wang et al., 2014; VandenBygaart et al., 2015). This resulted in a partially preserved but highly biologically processed SOC stock in terraced soils with a lower SPR relative to non-terraced soils. Soil redistribution during terrace development results in an exposure of the subsurface soil at the cut or eroding section, as well as burial of the original topsoil at the fill or depositional section. The terraced area of the study site is located in the middle and upper part of the hill. The pOSL signal showed that the terrace soil profiles gradually become older towards the bottom (Fig. 2), suggesting that the current terraces are most likely developed by stone lines which gradually catch soil material eroded from the summit. Our sampling strategy therefore mainly reflects the C stabilization mechanism of the depositional rather than the eroding part of the hill.
The significant relationship between SPR and total photon counts (Fig. 5a) indicates that the time since terracing is a key factor controlling the stability of SOC in terrace soils. More specifically, SPR declines rapidly with increasing terrace soil burial age until soils become relatively older, leading to an increase in SOC stock in the old terraces compared to the non-terraced landscape (Chen et al., 2020). In addition, we found that the percentage of unprotected (cPOM) and mineral-protected (S + C) SOC fraction is significantly related to the terrace soil burial age (Fig. 5b), indicating a shift from active SOC fractions with short residence times (higher SPR) at relatively younger burial ages to mineral-protected SOC fractions with long residence times (lower SPR) at relatively older burial ages. This clear shift to more processed recalcitrant SOC with age is the underlying process leading to SOC stabilization in terrace soils. By comparing the cPOM fraction of the topsoil layer (0–10 cm) with previous topsoil (burial horizon, > 60 cm), we estimated that about 23–27 % of the cPOM fraction in buried horizons has been decomposed or transferred into physical-protected or mineral-protected SOC since the terrace were built (Fig. 3b). Given that the buried soil horizons of terrace profiles still contain 1.7 times more unprotected SOC (cPOM) than SOC at similar soil depths in control profiles, we suggest that SOC cycling in the current terrace has not yet reached a steady state and that the SOC stock is most likely to slowly decrease due to cPOM decomposition in the future.
4.2 Main controls on temperature sensitivity
According to the Arrhenius equation, Q10 of SOC decomposition is theoretically jointly determined by the molecular complexity (SOC quality) and availability of the substrates (referred to here as SOC protection) (Davidson and Janssens, 2006). In general, enzymatic decomposition of biochemically recalcitrant substrates (lower SOC quality) requires more activation energy to degrade and should have a higher temperature sensitivity than the decomposition of more labile substrates (Bosatta and Ågren, 1999; Craine et al., 2010a). However, environmental constraints (SOC physical or chemical protection, soil acidity, etc.) can reduce substrate availability, dampening the intrinsic temperature sensitivity (Gillabel et al., 2010). It has been reported that soil pH is an important control on Q10 at the landscape scale by directly affecting microbial biomass, diversity, and therefore the enzyme activities or indirectly through altering nutrient solubility, mineral matrix, and therefore the substrate availability (e.g., Craine et al., 2010b; Ali et al., 2018). However, in our study soil pH was not strongly related to SPR or Q10 (Table 2) possibly due to the small variation in soil pH (pH = 3.71 ± 0.34). Instead, our results showed that at relatively younger burial ages, Q10 is negatively related to S + C-associated SOC fractions (Fig. 6) and clay content (Table 2). This indicates that the adsorption of labile SOC (e.g., dissolved OC) by soil-reactive clay minerals forms organo-mineral associations (SOC mineral protection) which reduce the substrate availability to decomposers (Kögel-Knabner et al., 2008). As a result, SOC mineral protection attenuates the intrinsic Q10, resulting in the rapid decrease in Q10 with total photo counts at the relatively young age stage. However, at relatively older soil burial stages, we could not detect any significant correlation between Q10 and SOC fractions (Fig. 5a), while C:N ratio of bulk soil, M, and S + C soil fractions were significantly related to Q10 (Table 2). More importantly, we observed a significant increase in C:N ratio for bulk soil and all SOC fractions at the oldest buried soil layers (Fig. 7). We proposed two possible reasons as to why C:N ratios were closely linked to Q10, especially in the oldest buried soil layers. Both the depth profile of soil chemical weathering, SOC concentration, and field investigation indicate that these oldest soil horizons (Fig. 7; total photon counts 1000 = 22.5) are likely to originate from the former buried topsoil (detailed in S1 in the Supplement). The former topsoil may still contain less decomposed organic litter, which is commonly reflected in a higher soil C:N ratio (Xia et al., 2021). Alternatively, unlike for fresh litter, SOC with a higher C:N ratio is usually considered as lower-quality or recalcitrant substrates which are less bioavailable for soil microorganisms (e.g., Sollins et al., 1996; Liu et al., 2017; Wang et al., 2018). The observed increase in soil C:N ratios at greater depths in older terraces might therefore reflect a shift towards poor-quality SOC substrates (Ali et al., 2018), which explains the observed increase in Q10 in the oldest soil horizons (i.e., Fig. 5a, Result 3.3). We propose that the latter is more likely in our experiments. Together, our results suggest that the factors controlling SOC temperature sensitivity of terrace soils (SOC mineral protection or C:N ratio) change over time. At relatively younger stages of soil burial, the reduction in substrate availability due to the increased SOC mineral protection with aging attenuates the intrinsic Q10 of SOC decomposition (Figs. 5a and 6), whereas at the oldest terrace soil burial age, SOC in buried layers reflects an increased Q10 probably due to (1) lower C quality (higher C:N ratio; Fig. 7) and (2) weaker SOC mineral protection (Fig. 5b; Table 2).
Terracing currently has buried a substantial amount of former topsoil SOC (De Blécourt et al., 2014). Our results show that although buried terrace soils contained 1.7 times more unprotected SOC (i.e., coarse particulate organic carbon) than non-terraced soils at comparable soil depths, a significantly lower potential soil respiration was observed relative to a control (non-terraced) profile. This suggests that the burial of former topsoil due to terracing provided a mechanism for enhanced C stabilization. Furthermore, we found that the evolution of SOC fractions along with terrace soil burial age is related to the depth patterns of specific soil respiration; i.e., there is a shift from active SOC fractions at relatively younger soil burial ages towards more processed recalcitrant SOC fractions at older soil burial ages.
Furthermore, our study provides empirical evidence for the drivers and basic patterns of the temperature sensitivity of SOC decomposition in agricultural terraces. We found that both the C:N ratio and SOC mineral protection regulate soil Q10. However, which mechanism predominantly controls soil Q10 depends on the age of the buried terrace soils. At relatively younger ages of soil burial, the reduction in substrate availability due to the increased SOC mineral protection with aging attenuates the intrinsic Q10 of SOC decomposition, whereas at older terrace soil burial ages, higher C:N ratios (poor C quality) result in an increased Q10 in deep horizons. It is expected that the ongoing evolution of SOC fractions and the associated changes in soil C:N ratio due to terrace aging will slowly but steadily destabilize buried former topsoil SOC.
All data used and produced in this study are available with the Supplement.
The supplement related to this article is available online at: https://doi.org/10.5194/bg-18-6301-2021-supplement.
PZ, KVO, SD, and AGB designed the study. CW, DC, DJF, PZ, AGB, LS, and AL excavated the terrace trench and collected soil samples. SC and PT performed the topography survey. AGB and KVO acquired the research funding. PZ wrote the original draft with input from all co-authors.
The contact author has declared that neither they nor their co-authors have any competing interests.
Publisher's note: Copernicus Publications remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
The authors would like to thank Ben R. Pears, Rosa Maria Albert, Inger Alsos, Kevin Walsh, and the volunteers who helped with the field excavation in Ingram Valley, UK. The authors also thank Marco Bravin for his assistance with the SOC sample analysis.
This research has been financially supported by the European Research Council, H2020 (grant no. TerrACE (787790)). Pengzhi Zhao has been supported by the joint grant from the China Scholarship Council and UCLouvain (no. 201706600009). Kristof Van Oost is a research director of the FNRS Belgium.
This paper was edited by Jianming Xu and reviewed by two anonymous referees.
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