Changes of Soil Organic Carbon after Wildﬁre in a Boreal Forest, Northeast CHINA

: Boreal forests with high carbon sequestration capacity play a crucial role in mitigating global climate change. Addressing dynamic changes of soil organic carbon (SOC) after wildﬁre helps in understanding carbon cycling. The objective of this study is to investigate changes in soil organic carbon after wildﬁres in a boreal forest. The post-ﬁre soil chronosequence after 3 months, 17 years, and 25 years within a boreal forest was used to examine dynamic and stable SOC after wildﬁre at the decadal scale. Soils in genetic horizons were sampled and analyzed for dynamic and stable SOC, including water stable aggregates (WSA), WSA associated organic carbon (WSA-SOC), soil heavy fractions (HF) associated organic carbon (HF-SOC), and soil total organic carbon (TOC). The TOC and WSA-SOC content of the A horizon was the greatest in the control site. There was no signiﬁcant difference for TOC between burned and unburned deep BC horizons. The TOC for the A and B horizons at the 17-year-old site was signiﬁcantly lower compared to the other sites. TOC did not recover to the pre-ﬁre levels (control site) in any of the burned areas. The lowest WSA was found in the A and B horizons of the 3-month-old site. The WSA at the 25-year-old site was higher compared to the 17-year-old site. WSA increased with time following ﬁre, but the recovery rate differed among different sites. The lowest concentration of WSA-SOC for the A horizon occurred at the 17-year-old site, and no signiﬁcant difference was observed between B and BC horizons. The HF content for the A horizon was the greatest at the 3-month-old site. There was no signiﬁcant difference in HF-SOC between B and BC horizons in all sites. TOC and stable SOC (HF and WSA) increased over time in species-dominance relay stand areas, while self-replacement stands areas showed the opposite. The results indicate that overall, the ability of soil to sequester carbon decreased after wildﬁre disturbances. Stable SOC accumulated more in areas where species-dominance relay succession occurred compared to the self-replacement stands. These disturbances were more pronounced for surface soil horizons. This study provides a quantitative assessment of SOC changes after wildfires that are useful for forest management and modeling forecasts of SOC stocks, especially in boreal forests.


Introduction
Boreal forest soils play an important role in the global carbon cycle. The amount of carbon stored in forests soils is controlled by the carbon input from vegetation leaves and roots, and by soils, which can store vast quantities of organic carbon [1,2]. Boreal forests show high soil organic carbon (SOC) sequestration due to their large woody biomass, extensive roots, and abundant leaf litter, while the mineralization rate of organic carbon is relatively slow due to poor drainage and low temperatures [3,4]. Boreal forests are important to alleviate global warming by preferentially increasing the fungal mineralization of slow-turnover carbon pools in boreal organic soils [5]. Boreal forest can also be a significant contributor to the atmospheric CO 2 from above and underground biomass burning [6]. A recent review [7] points to the importance of underground biomass burning (smoldering) as a significant contributor to atmospheric CO 2 .
Analyzing post-fire succession is important to understand boreal forest dynamics and how it affects SOC. Forest fires change the composition of species in the local ecosystem [8,9] and affect the establishment and development of wooded areas across landscapes [10]. In the Greater Higgnan Mountains region, tree regeneration after wildfires has two major ecological succession pathways; self-replacement and species-dominance relay. Self-replacement is the condition under which dominant tree species of pre-fire canopy that was burned by a fire naturally recovers as the dominant canopy species. In contrast, species-dominance relay occurs when different tree species successively assume canopy dominance following fire [11]. Both successional pathways are important for the development of forest composition and influence the potential response of boreal forests to future disturbances and climate change. Generally, burned areas in the Greater Higgnan Mountains region develop into secondary succession after severe fire disturbance [12]. The succession type depends on whether there is a birch (Betula platyphylla) invasion. If the habitat conditions are suitable for a birch invasion, community succession occurs. Then larch (Larix gmelinii) forests develop to replace birch tree species until larch forest formation reaches a climax. If birch seeds do not spread to fire-affected areas, only single larch forest self-replacement will occur after severe fire disturbance in the Greater Higgnan Mountains region [12]. During re-vegetation and plant succession, carbon accumulates both in the biomass and the soil [13,14]. After a wildfire, reforestation accelerates the conversion of the fire-affected areas from carbon source to carbon sink [15], although natural regeneration may also increase carbon sequestration [16].
SOC stabilization includes chemical stabilization, biochemical stabilization, and physical protection. The accumulation of SOC due to physical protection is a result of the influence of aggregation in the formation of fracture planes (the sides of aggregates connected by cementing agents), which act as barriers to microbial action [17]. Soil aggregates are important agents in SOC retention and protection from decomposition [18,19]. The soil aggregation process and aggregate stability are affected by land management and disturbances [20,21]. Soil aggregates have been reported to increase with re-vegetation in a landslide area [22] and nitrogen fertilization in prairie regions [23]. However, studies on the effects of fire on soil aggregates in forests have shown opposite results [24,25]. Mataix-Solera et al. suggested that the effects of fire on soil aggregation depend on fire intensity and its influence on aggregation-related properties such as soil organic matter, water repellency, mineral compositions, and soil microorganisms [24]. The soil light fractions' (LF) and soil heavy fractions' (HF) associated organic carbon (LF-SOC and HF-SOC), was determined using the density fractionation method as described by Gregorich and Ellert (1993).They are useful to identify specific carbon pools and evaluate their responses to soil management strategies which involve controlling SOC [26] and characterizing soil quality for sustainable land use [27]. Heavy fractions (HF) are more stable and contain greater processed SOC [28,29], while high-density organo-mineral fractions have lower carbon concentrations [30]. HF is a major carbon sink [31] that can lead to poor soil respiration [32]. Both soil stable carbon fractions are indicative of soil capability to sequester carbon.
The objective of this study is to investigate changes in soil organic carbon after wildfires in Larix gmelinii forests. TOC and soil stable carbon fractions, aggregate-associated organic carbon (WSA-SOC), and heavy fraction organic carbon (HF-SOC) were determined both in the surface and the subsurface horizons. We hypothesized that the SOC pool and its physical fraction following wildfires decreased due to the combustion of soil organic matter, and that SOC levels would begin to recover following re-vegetation through stand development.

The Study Area
The study area is located in the Greater Higgnan Mountains region, northeastern China (N 50 • 10 ~53 • 33 , E 121 • 12 ~127 • 00 ). It covers an area of 84,600 ha [33]. This region belongs to the cold temperate zone and has a cool continental climate with hot-wet summer and cold-snowy winter. The mean annual temperature and precipitation are −4 • C and 400-500 mm, respectively. The dry spring and high winds promote conditions for forest fires. The dominant tree species in the study area is Larix gmelinii, while other prevalent tree species are Pinus sylvestris var mongolica, Picea koraiensis, Betula platyphylla, Quercus mongolica, and Populus davidiana. Shrubs include Rhododendron dauricum, Vaccinium vitisidaea, Ledum palustre, and Lespedeza bicolor. The parent material in the study area is primarily igneous rock resulting in igneous residuum soils or soil formed from igneous rock colluvium. The predominant soils can be classified as Cambisols according to the Keys to Chinese Soil Taxonomy (3rd edition) [34] and World Reference Base [35], and Inceptisols according to the US Soil Taxonomy [36].
The Greater Higgnan Mountains region is the worst-hit area from forest fires in China. During the 1970 to 2006 period, forest fires occurred on average 27.8 times a year with an annual average burned forest cover area of 7.5 × 10 4 ha. Three types of causes of fires were identified: lightning, human-caused, and unknown [37], typically occurring between April and June. Since the 1990s, the annual amount of forest fires has shown an increasing trend, affected most likely by a combination of increased global temperatures and human activities, including accidental fires [33,38].

Soil Sampling
Three independent sites were sampled that had experienced high-intensity fires at different times (3 months prior, 17 years prior, and 25 years prior) and have a similar soil genesis history all occurring within the Greater Higgnan Mountains region. After wildfires, soils on both plant succession types of species dominant relay (the larch forest was replaced by an early-seral community of small-leaved trees) and self-replacement (the larch forest replaces itself rapidly) were sampled. The soil in an area where no records of fire occurred for over 30 years was selected as the background control (Table 1). Fire intensity was estimated by comparing remote sensing images before and after fire using the Composite Burn Index (CBI) records [39]. To minimize the effects of site conditions, especially erosion, on SOC and stable SOC, areas on flat slopes of less than 3 • were selected. The soils have developed from igneous rock and are described as well-drained and greater than 50 cm in thickness, are the most dominant site type of this area. Each selected region had similar soil-topographic characteristics. Soil profiles were excavated in the center of each plot. A square plot of 20 m × 20 m was selected within each region and three random soil profiles were excavated in each square plot. Soils were described and sampled according to the standard procedures described in the "Field Book for Describing and Sampling Soils, version 3.0" [40].

Soil Analysis
Soil samples were air-dried in the laboratory and the moisture content of samples was determined by the oven-dry method (105 • C for 12 h). Stones and plant roots were removed with a 2 mm sieve. Mineral soil samples were ground in an agate mortar and sieved in a 0.149 mm sieve. The size distribution of the water stable aggregates (WSA) was measured by wet sieving [41] with a soil aggregate analyzer (DM200 Shanghai, China). A 100 g sample of airdried bulk soil (passed through a 6.75 mm sieve) was placed on top of a set of nested sieves (2000, 250, and 53 µm) [18]. Nested sieves were placed in a bucket that was slowly filled with deionized water (poured along the edge to minimize disturbance) until the uppermost sieve touched the water. Aggregates were slowly wet through capillary action over 30 min time intervals. After being submerged for 5 min at room temperature, the nested sieves were gently oscillated (5 cm amplitude and 25 strokes min −1 ) within a column of water for 30 min. Following, different sized WSA were gently backwashed off the sieve into an aluminum pan. Floating organic material (>2 mm) was removed and discarded because large organic material is not considered as soil organic matter. Aggregates were oven-dried (60 • C) to constant moisture content, weighed, and stored in glass jars at room temperature. WSA were classified into macro (>2.0 mm and 0.25~2.0 mm) and micro (0.053~0.25 mm and <0.053 mm) size classes, and relative abundance was expressed as dry weight to the total sample (100 g). The WSA-SOC concentration in each fraction of >2000 µm, 250-2000 µm, 53-250 µm, and <53 µm were measured, respectively.
Water stable aggregates (WSA) were calculated as follows [17]: where WSA = water stable aggregates (%), wi = weight of the aggregate fraction, w = total weight of sample used. Soil aggregates were classified into macro (>2000 µm and 250~2000 µm) and micro (53~250 µm and <53 µm) size classes, and their relative abundance in each category was expressed as a percentage of the total sample. The WSA-SOC content (g) was calculated as the WSA-SOC concentration multiply by the weight of each size fraction of WSA.

Density Fractionation of SOC
Soil heavy fractions (HF) were determined using the density fractionation method as described by Gregorich and Ellert [42]. In brief, air-dried soil (5 g) was placed in a 50 mL conical centrifuge tube with 35 mL NaI solution (1.7 g cm −3 ) and gently stirred with a glass rod. Samples were ultrasonicated at 250 W for 20 min with a KQ-250E sonicator (Kunshan Ultrasonic Instrument Company, China), then filtered through a 0.45 µm filter. The light fractions (LF) retained on the filter were rinsed with 100 mL 0.01 M CaCl 2 and then with 200 mL deionized water to remove the NaI and CaCl 2 . Sediment from the centrifuge tubes was re-suspended in NaI by gently stirring with a glass rod. The procedure was repeated twice. The three sub-fractions were combined and oven-dried at 50 • C for the LF. The HF were rinsed twice with 100 mL deionized water, and the remaining soil after rinsing was dried at 50 • C for 8 h and weighed [43]. The HF-SOC concentration in the HF fraction was subsequently measured. The HF-SOC content (g) was calculated as the HF-SOC concentration multiply by the weight of HF.

Chemical and SOC Sample Analysis
The pH (H 2 O) and pH (KCl) were determined by the 1:2.5 ratio of soil to water or the saturated KCl solution. The soil total-nitrogen (N) and soil total organic carbon of mineral soil samples TOC, WSA-SOC, and HF-SOC were determined by the dry combustion method using an Elemantar Vario III (Elementar, https://www.elementar.com/ (accessed on 17 August 2021)).

Statistical Analysis
The difference among TOC concentrations, abundance of WSA, WSA-SOC, and HF-SOC in mineral horizons was analyzed using a one-way analysis of variance. Data was analyzed using Sigmaplot 12.5 and SPSS 13.0.

The Soil Properties
Wildfires profoundly influenced the development and succession of the forest ecosystem. Species-dominance relay succession occurred at the 25-year-old site (25 years after fire disturbance), where deciduous trees (especially Betula platyphylla) had colonized the area. Self-replacement succession occurred at the 17-year-old site (17 years after fire disturbance), where Larix gmelinii dominated. The type of vegetation after wildfire clearly influenced canopy density ranging from 0.2 to 0.7 ( Table 1).
The basic characterization of mineral soil with depth is provided in Table 2. Dry samples were mostly yellow-orange or pinkish-white in color, while wet samples were brown, dark brown or yellow-brown. The texture of surface layers was loam and silt loam, while the sub-surface horizons were primarily clay loam and sandy loam. The soil structure was granular in A horizon at all sites except for the 3month-old site, where the structure was more blocky than granular ( Table 2). The B and BC horizons were described as having a blocky structure. The bulk density of the surface soil from the fires was, on average, smaller than control. The pH (H 2 O) and pH (KCl) of horizons in the soil profiles after wildfire was higher compared to the control, and the levels at the 17-year-old site were significantly greater than that of the 25-year-old site. The total-nitrogen (N) level was greatest in the control site, and the 25-year-old site had a greater N level than that of the 17-year-old site.

Soil Total Organic Carbon (TOC) Concentration of Mineral Horizons
Overall, TOC concentration ( Figure 1a) and SOC stocks ( Figure 1b) decreased with soil depth. The SOC concentration for the Ah horizon in the control site was significantly greater than the other succession sites, and the 17-year-old site was significantly lower than the other sites for both the Ah and B horizons. There was no significant difference between burned and unburned deep BC horizons. As expected, the rate of decrease of SOC stocks was not as pronounced compared to the SOC concentrations. This is likely due to the higher soil bulk density values for the subsurface horizons compared to the subsurface horizons and thicker subsurface horizons (Table 2).

Water Stable Aggregates (WSA) and Associated SOC (WSA-SOC) Concentrations and Stocks
The variation of WSA showed that the WSA abundance in the A horizon was significantly affected by fire ( Figure 2a). The WSA content in different soil horizons was the greatest in the control site, while the 25-year-old site had greater levels than the 17-year-old site. The lowest WSA was found in the A and B horizons of the 3-month-old site. WSA increased with recovery time following fire, but the recovery degree differed among different sites. The abundance of WSA >2000 μm and 250-2000 μm in A and B horizons of the 25-year-old site was significantly greater compared to 53-250 μm and <53 μm aggregate sizes following a wildfire. However, the opposite was true for the 17-year-old site (Figure 2a).
The greatest concentration of aggregate-associated SOC of the A horizon was in the control site, and the lowest appeared in the 17-year-old site. There was no significant difference in aggregate-associated SOC between the B and BC horizons (Figure 2b).

Water Stable Aggregates (WSA) and Associated SOC (WSA-SOC) Concentrations and Stocks
The variation of WSA showed that the WSA abundance in the A horizon was significantly affected by fire ( Figure 2a). The WSA content in different soil horizons was the greatest in the control site, while the 25-year-old site had greater levels than the 17-year-old site. The lowest WSA was found in the A and B horizons of the 3-month-old site. WSA increased with recovery time following fire, but the recovery degree differed among different sites. The abundance of WSA >2000 µm and 250-2000 µm in A and B horizons of the 25-year-old site was significantly greater compared to 53-250 µm and <53 µm aggregate sizes following a wildfire. However, the opposite was true for the 17-year-old site (Figure 2a).
The greatest concentration of aggregate-associated SOC of the A horizon was in the control site, and the lowest appeared in the 17-year-old site. There was no significant difference in aggregate-associated SOC between the B and BC horizons (Figure 2b).

The Heavy Fraction Soil Organic Carbon (HF-SOC) Concentration and Stocks
For the Ah and B horizons, both the HF-SOC concentrations ( Figure 4a) and stocks (Figure 4b) in the 17-year-old site were significantly lower than the other sites. There was no significant difference in HF-SOC between B and BC horizons for all sites.

The Heavy Fraction Soil Organic Carbon (HF-SOC) Concentration and Stocks
For the Ah and B horizons, both the HF-SOC concentrations ( Figure 4a) and stocks (Figure 4b) in the 17-year-old site were significantly lower than the other sites. There was no significant difference in HF-SOC between B and BC horizons for all sites.

The Heavy Fraction Soil Organic Carbon (HF-SOC) Concentration and Stocks
For the Ah and B horizons, both the HF-SOC concentrations ( Figure 4a) and stocks (Figure 4b) in the 17-year-old site were significantly lower than the other sites. There was no significant difference in HF-SOC between B and BC horizons for all sites.

Variability of Basic Soil Properties after Wildfire
The direct effect of fires on soil properties included physical changes and indirect effects from habitat changes following wildfires [17]. The plant succession may have had a strong influence on improving soil structure. The SOM consumed by fire initially resulted in the breakdown of the granular structure and the hardening of the surface from rainfall leading to small differences in bulk density values between surface and sub-surface horizons compared to the unburned site. The increase in bulk density often associated with wildfire is due to the destruction and alteration of SOM by heating [44], leading to changes in soil porosity and permeability. The pH (H 2 O) and pH (KCl) of the soil with depth also increased after fire, most likely as the result of released basic cations from the burning of the organic material [45]. Soil organic N was likely lost immediately upon heating due to volatilization, as found by other workers [44]. Moderate to high-intensity fires convert most soil organic N to inorganic forms. The 25-year-old site had greater organic N levels than the 17-year-old site. This may be attributed to the accumulation of N-rich litter and fine root turnover [46], although the rate of recovery in N decreases with succession from N-rich Populus to N-poor Picea. Fire disturbance had no obvious effect on soil color and texture, but directly destroyed soil structure resulting in decreased soil porosity and increased soil bulk density.

Variability of TOC after Wildfire
Almost all organic layers were burned off by the severe wildfire, according to field investigations. The TOC concentration of soil mineral samples from pedogenic horizons decreased with depth (Figure 1a,b). The TOC concentration of the Ah horizon in the control site was the greatest. SOC was reduced to a small amount of black carbon that was resistant to decomposition under the immediate influence of severe wildfire disturbance, associated with the release of a large amount of carbon dioxide [17]. This likely reduced the overall SOC concentration in the soil. After the wildfire, a large number of herbaceous plants germinated, to be succeeded by the shrubs. Most likely, a succession of vegetation sequences of herbaceous plants was followed by pioneer species invasion after the fire and may have led to a transition of community structure from the original coniferous forest to the broadleaf mixed forest or the broad-leaved forest as observed by others [9]; this likely resulted in litter increase and accumulation. As a result, TOC concentrations increased, for example, at the 25-year-old site, and especially for the topsoil TOC, which was comparable with the TOC levels at the control site. However, in general, TOC did not recover to the levels of the control site in any of the sampling locations. Over time, TOC increased for all sites, but at different rates and levels, as shown by the results at the 25-year-old site compared to the 17-year-old site, especially for the Ah horizon. Nevertheless, because of different site conditions, especially with regard to community succession, the TOC levels at the 17-year-old site will likely not reach that of the 25-year-old site. TOC concentrations increased over time in species-dominance relay areas at the 25-year-old site due to the growth of invasive broad-leaved forest vegetation, dense canopy, and large amounts of accumulated litter (Table 1). In contrast, self-replacement at the 17-year-old site resulted in decreased TOC levels. Because of the slow rate of self-renewal and the low amount of litter, the TOC accumulated in the soil at slower rates. On the other hand, due to a slower increase of canopy density and a large amount of solar radiation absorbed by the ground surface, the TOC would likely be easily decomposed. Other investigators have made similar observations [47,48]. Species-dominance relay succession at the 25-year-old site led to greater TOC accumulation for the B horizons due to larger above and below-ground biomass associated with the broadleaf trees (Table 2) [49,50].
Initially, the increased soil bulk density and likely decrease of soil hydraulic conductivity in the A horizons (Table 2) reduced leaching and deposition of SOC to the subsurface horizons. For example, even after 17 years of recovery, the TOC content in the B horizon was lower than that of the control site. This was also obvious for the 3-month-old site.
Over time, the improvement of soil conditions was beneficial for SOC accumulation and stabilization in the B horizon. For example, the presence of clay coatings at the 25-yearold site compared to other sites supports strong pedogenic processes such as leaching of clay-bound organic matter from A to B horizons. Thus, the TOC content for the B horizon was greater at the 25-year-old site compared to the control site. However, there was no difference in the deep BC horizons between different sites. This indicated that the effect of fire on TOC decreases with soil depth, as documented by previous research [43]. However, research has shown that smoldering and slow-burning fires can significantly affect TOC distribution with depth [51,52].

Variability of Water Stable Soil Aggregates (WSA) and Associated SOC (WSA-SOC) after Wildfire
Soil aggregates associated SOC was the main component of soil organic carbon. The content of WSA in different horizons was greater at the control site. In addition, macro-aggregate content > 2.0 mm in the A horizons did not appear to decrease after fire at the 3-month-old site. This heat-induced aggregation following wildfire has been attributed to the dehydration of soil gels and thermal transformations of the cemented iron and aluminum oxides at temperatures >220 • C [53]. A combination of macroaggregate formation after the wildfire [17] with higher associated SOM initially leads to increases of the aggregate associated SOC, especially for the macroaggregates, as observed in our study. As a result, the 3-month-old site had a greater macroaggregate associated SOC than 25-year-old site. However, this part of the organic carbon is not stable due to continued changes of the habitat conditions and smoldering after the fire, which likely could destroy these aggregates. Research has shown that underground fires, especially smoldering of underground biomass, can lead to further losses and destabilization of SOC [6,7].
Overall, the soil aggregate associated SOC in the Ah horizon at fire-affected sites was lower when compared to the control site. The wildfire had partly consumed aggregate associated SOC, which did not recover to the original level along the chronosequence of 25-year-old plant succession. However, leaf litter and roots from broadleaf tree species led to greater soil aggregation compared to coniferous trees. The growth of invasive broadleaved forest vegetation, dense canopy, and large amounts of accumulated litter resulted in greater levels of SOC and likely contributed to the macroaggregates formation at the 25-year-old site and the increased macroaggregate associated SOC. While at the 17-year-old coniferous forest site with a slow rate of self-renewal, a slow increase of canopy density, a low amount of litter, and microbial activity may have led to a decrease of macroaggregates and macroaggregate associated SOC [54,55].

Variability of Soil Heavy Fractions (HF) and Associated SOC (HF-SOC) after Wildfire
The post-fire soil chronosequence was used to examine long-term dynamics of SOC and stable organic carbon (WSA-SOC and HF-SOC) of boreal forests after wildfire at the decadal scale. The HF is composed of invisible organic materials which are tightly bound to soil minerals to form the primary organo-mineral complexes [56,57]. Ashagrie et al. reported that 60-90% of TOC is in the form of HF-SOC dominating the soil organic carbon pool [56,[58][59][60][61]. These findings explain the similar trend that HF-SOC and TOC showed for the A horizons. The concentration of the HF-SOC in the A horizons was the greatest in the 3-month-old site, presumably due to the effects on soil gels and thermal transformation of the cemented iron and aluminum oxides [53]. After fire, there was not adequate organic carbon to support the canopy at 17-year-old self-replacement site. Thus organo-mineral complexes were more easily decomposed by exposure to rain, which decreased the HF contents in A and B horizons. In contrast, the HF-SOC increased at the 25-year-old relay succession site due to the increased organic carbon inputs by broadleaf above and below ground biomass. The physical fractions of soil stable organic carbon increased over time at the 25-year-old relay succession sites, where carbon sequestration potential and capacity are larger compared to the 17-year-old self-replacement succession site.
However, none of the two succession types led to a full recovery of the soil stable carbon contents to the levels of unburned forests. Therefore, the stand-replacing fire can weaken soil carbon sequestration ability. The stable SOC accumulated more in areas where species-dominance relay succession occurred after stand-replacing fires than that in the self-replacement areas. Species-dominance relay succession allowed for invasive broadleaved forest vegetation to establish a dense canopy under which large amounts of litter could accumulate. When self-replacement succession occurred, the canopy density was less compared to species-dominance relay succession, and stable SOC contents decreased over time. The soil carbon sequestration capacity was greater for the species-dominance relay succession.

Conclusions
Past soil color and texture change little following the wildfire, while soil structure degraded significantly leading to decreased soil porosity and increased soil bulk density. The soil under species-dominance relay succession showed a greater carbon sequestration capacity and potential. At the decadal scale, the TOC and stable SOC (WSA and HF) could not recover to the levels of the control site in any area due to stand-replacing fire. SOC and stable SOC increased over time in species-dominance relay areas, while self-replacement ones showed the opposite results. WSA-SOC increased over time following fire, but the recovery rate differed among sites. Changes in physical and biochemical characteristics of organic inputs, re-vegetation, and canopy after wildfire were responsible for the observed SOC differences and dynamics. The ability of soil to sequester carbon decreased after wildfire disturbances. These disturbances were more pronounced for surface soil horizons. This study provides a quantitative assessment of SOC changes after wildfires that are useful for forest management and modeling forecasts of SOC stocks, especially in boreal forests. However, our study was limited to a boreal forest ecosystem, and studies on other forest ecosystems are needed.