The present study was carried out in the Nature Reserve of Shanyutan, which is the larger intertidal wetlands in the Minjiang estuary, Fujian Province, Southeastern China (119°34′12″ – 119°41′40″E, 26°00′36″ – 26°03′42″N, Figure 1 ). The climate here belongs to the typically subtropical monsoon climate, and the annual mean rainfall and temperature are approximately 1300 mm and 19°C, respectively (Mou et al., 2018). The area has enriched vegetation types, and the predominant native species contain Scirpus triqueter, Cyperus malaccensis, and Phragmites australis, which mainly grow in low, middle, and high intertidal zones, respectively (Gao et al., 2017). In 2002, the S. alterniflora was introduced to the study area, expanded rapidly, and occupied native C. malaccensis habitat where in the middle intertidal zone for the next 20 years (Mou et al., 2014).

The superimposition analysis of the Landsat 8 image (2014), SPOT5 image (2010), and aerial image (2006) were used to identify the sampling location with different chronosequences of invasive S. alterniflora (Jin et al., 2017). The locations of sample collection included a native habitat (CM, C. malaccensis) and three invasive S. alterniflora habitats that replaced the former in 2010 – 2014 (SA-6), 2006 – 2010 (SA-10), and 2002 – 2006 (SA-14), respectively ( Figure 1 ). The above-mentioned four habitats were chosen as sample points, and these represent the different invasion degrees of S. alterniflora. Over the past several years, the study area was noticeably divided by a tidal creek, and the CM habitats on the east/northeast/north side of the creek have been occupied by this invasive plant ( Figure 1 ). Thus, the sampling location of CM habitats in our study was situated in another side of the creek. These sampling locations (CM, SA-6, SA-10, and SA-14) were situated in the middle intertidal zone, which had similar sediment and hydrodynamic characteristics before S. alternifolia invasion. Since a large portion of the root biomass of S. alterniflora is distributed within a depth of 0 – 20 cm, where the sediment has higher TOC contents and is more susceptible to environmental changes (Tong et al., 2011; Jin et al., 2017), this depth was chosen to explore the response of organic carbon mineralization dynamics to S. alterniflora invasion. In each sampling habitat, three sediment samples at two depths (0 – 10 cm and 10 –20 cm) were collected randomly based on a stainless steel sediment cylinder (10 cm diameter) on July 23, 2016, and December 22, 2016 from approximately 7:00 to 9:00, during the diurnal ebb-tide. Sediment temperatures were recorded immediately based on a portable sediment thermometer. After removing plant roots, residues, and recognizable stones, the samples were put into sterile ziplock bags. Then, sediment samples were stored in a thermostat at approximately 4 °C and returned to the analyzer room within 4 h. After that, sediment samples were homogenized and separated into two fractions: one fraction was stored at 4 °C to measure sediment MBC and DOC contents, and the second fraction was freeze-dried for determination of other carbon fractions (TOC and EOC) and geochemical variables as well as organic carbon mineralization dynamics.

The portable thermometer was used to measure sediment temperatures. The pH and electrical conductivity (EC) of sediment were determined by the handheld pH (IQ Scientific Instruments, USA) and EC tester (Spectrum Technologies Inc., USA), respectively (Gao et al., 2017). The oven-drying and cutting-ring methods were used to analyze sediment moisture and density, respectively. Total nitrogen (TN) contents were measured based on a CHNS analyzer (Vario EL, Elementar, Germany) (Jin et al., 2017). The potassium chloride solution (KCl) of 2 M was applied to extract sediment ammonium (NH₄ ⁺), nitrate (NO₃ ^–) and nitrite (NO₂ ^–), and their contents were measured by an automatic injection analyzer (Skalar SAN++, the Netherlands) (Mou et al., 2018).

Sediment TOC contents were analyzed based on a CHNS analyzer (Vario EL, Elementar, Germany) after 1 M hydrochloric acid (HCl) acidification (Jin et al., 2017). The methods of chloroform fumigation extraction were used to determine MBC content in sediment (Song et al., 2012). In brief, two fresh sediment samples (10 g) were placed into 100 mL beakers, and these samples were incubated for 24 h in a dark fumigation dish, with one of them being fumigated with chloroform. The sediments with and without fumigation were extracted with 40 mL potassium sulfate (K₂SO₄) (0.5 M), and the mixed solutions were filtered through a 0.45-µm filter membrane. Subsequently, TOC concentration in the filtrate was measured by a TOC analyzer (TOC-V_CPH, Shimadzu). Sediment MBC contents were calculated based on the TOC concentration in the filtrate with and without fumigation (Song et al., 2012). Sediment DOC contents were measured by a TOC analyzer (TOC-V_CPH, Shimadzu) after extraction with deionized water (Liu et al., 2022). The EOC contents in sediment were quantified based on the potassium permanganate (KMnO₄) oxidation method (Song et al., 2012). Freeze-dried sediment samples (1 g) were extracted with 333 M KMnO₄ solution (25 mL), and the supernatant was collected after 3 h standing. Then, the absorbance in the supernatant at 565 nm was determined based on the UV-Vis spectrophotometers (UV-2450, Shimadzu). Meanwhile, the blank sample without sediment was also included in the analysis. Sediment EOC contents were estimated according to the KMnO₄ concentrations in sediment and blank samples.

A series of incubation experiments were designed to study the impacts of invasive S. alterniflora on organic carbon mineralization dynamics. Freeze-dried sediment samples of 20 g were put into 120 mL glass vials equipped with two triple valves, and they were pre-wetted to approximately 60 ± 3% water-holding capacity. All glass vials were preincubated in a thermostatic incubator for 7 days to restore microbial activities before closed incubation. Then, these glass vials were incubated at a constant temperature (summer: 32°C, winter: 17°C) in the dark incubator, and the organic carbon mineralization rates on days 1, 3, 5, 7, 10, 14, 21, 28, 38 and 56 were determined. On each sampling date, the incubation glass vials were flushed with high-purity nitrogen gas through three-way stopcocks for 5 min, and the 3 mL gas samples (initial values) were collected immediately after closed. After 24 h incubation, gas samples (3 mL) were obtained again via a sterile injector, and these were marked as final values. The gas chromatograph (GC-2014, Shimadzu) was used to measure the carbon dioxide (CO₂) concentrations in collected gas, and the organic carbon mineralization rates at each incubation day were calculated based on initial and final CO₂ concentrations in the headspace of glass vilas (Equation (1)) (Mou et al., 2018):

where F is sediment organic carbon mineralization rates (μg g^-1 d^-1); d c d t represents the changes in CO₂ concentrations (μL L^-1 h^-1). The headspace volume of the incubation glass vila (L) and the sediment weight (g) were expressed as V_H and M_S , respectively. The M_V and M_W refer to the molecular volume(L mol^-1) and weight (g mol^-1) in an ideal gas, respectively; T is the temperature across the incubation period (°C). In addition, a first-order kinetic model was applied to determine the mineralization kinetics and characteristics of organic carbon, which was calculated by Equation (2) (Cooper et al., 2011):

where C _t is the cumulative carbon mineralization amounts at time t (mg g^-1). The C ₀ denotes potential carbon mineralization amounts (mg g^-1). The t represents incubation days (d), and k is the carbon mineralization rate constant.

All analysis was conducted based on the SPSS 19.0 and Origin 2021 software package. These data were examined for normal distribution and the need for any necessary transformations before statistical analysis. The one-way analysis of variance followed by the LSD was conducted to detect the statistical differences in sediment organic carbon fractions across four habitats in the same season. A first-order kinetic model in Origin 2021 was used to estimate the potential carbon mineralization amounts and the mineralization rate constant. Pearson’s related analysis was performed to reveal the associations between sediment geochemical properties, organic carbon fractions, and their mineralization dynamics.

Sediment temperature varied from 16.80 to 33.83°C, and summer temperature (32.95 ± 1.09°C) was significantly higher than that in winter (17.28 ± 0.47°C) (p< 0.05, Table 1 ). In summer, the highest and lowest temperatures of sediment occurred in SA-10 and SA-6 habitats, respectively, but there were no statistical differences across different habitats in winter (p > 0.05, Table 1 ). Sediment pH in summer ranged from 5.18 − 5.91, which was highest in SA-6 habitats, followed by the CM habitats, and lowest in the SA-14 and SA-10 habitats. While in winter, sediment pH was significantly higher in S. alterniflora habitats (SA-14, SA-6, and SA-10) than in C. malaccensis habitat (CM) (p< 0.05). No obvious differences in pH were observed between 0 − 10 cm and 10 − 20 cm depth ( Table 1 ). Sediment EC in summer and winter ranged from 0.70 to 1.73 and 2.17 to 2.91, respectively, and the highest values were observed in SA-14 habitats ( Table 1 ). In summer, sediment water content (37.09 − 50.68%) and bulk density (1.31 − 1.67 g cm^-3) were generally lower and higher respectively, in C. malaccensis habitat (CM) as compared to S. alterniflora habitats (SA-14, SA-10 and SA-6), but the values did not present similar change patterns in winter ( Table 1 ). Sediment TN, NH₄ ⁺, NO₃ ⁻ and NO₂ ⁻ contents were in the range of 1.60 − 2.30 g kg^-1, 21.61 − 48.89 mg kg^-1, 0.78 − 1.72 mg kg^-1 and 12.06 − 34.27 μg kg^-1, and their values generally increased with the invasion degree of S. alterniflora ( Table 1 ). Additionally, sediment TN, NH₄ ⁺, NO₃ ⁻ and NO₂ ⁻ contents at the surface (0 − 10 cm) were higher than those at the subsurface (10 − 20 cm), except for winter NH₄ ⁺ in SA-10 and SA-14 habitats ( Table 1 ).

Sediment TOC contents varied from 11.33 to 30.51 g kg^-1, and S. alterniflora invasion generally increased the values, especially in SA-10 and SA-14 habitats ( Figure 2 ). In CM habitats, TOC contents at 0 − 10 cm sediment layer were larger than those at 10 − 20 cm sediment layer, but no obvious changes were observed between the two sediment layers in S. alterniflora habitats (SA-14, SA-10, and SA-6) (p > 0.05). Seasonally, sediment TOC contents were higher in summer than in winter in these four habitats ( Figure 2 ). The changes in sediment MBC contents varied among four habitats at different depths. Wherein, sediment MBC contents at the surface (0 − 10 cm) were significantly higher in SA-14 and SA-10 habitats than in CM habitats both in summer and winter ( Figure 2 ) (p< 0.05). While at 10 − 20 cm depth, summer sediment MBC did not differ among four habitats (p > 0.05), but highest values were observed in SA-14 habitats in winter. Sediment DOC contents ranged from 74.89 to 113.47 mg kg^-1, and summer sediment DOC contents in S. alterniflora habitats (SA-14, SA-10, and SA-6) were generally higher than in C. malaccensis habitat (CM), but no statistical differences across different habitats in winter ( Figure 2 ) (p > 0.05). The DOC contents at 0 − 10 cm sediment layer were higher than those at 10 − 20 cm sediment layer both in summer and winter. In addition, no obvious seasonal differences in sediment DOC contents were found among four different habitats (p > 0.05). The EOC contents varied from 3.87 to 8.53 g kg^-1, and the values in SA-10 and SA-14 habitats were higher than those in SA-6 and CM habitats, although some differences did not reach a level of statistical significance ( Figure 2 ). Sediment EOC contents at the surface (0 − 10 cm) were also higher than those at the subsurface (10 − 20 cm). The EOC contents with little variation between summer and winter in CM and SA-6 habitats, while the values in summer were larger than those in winter in SA-14 and SA-10 habitats ( Figure 2 ).

The mineralization rates of sediment organic carbon in SA-14, SA-10, SA-6, and were in the range of 64.22 − 770.99 μg g^-1 d^-1, 65.21 − 624.82 μg g^-1 d^-1, 64.73 − 420.16 μg g^-1 d^-1, and 60.97 − 362.45 μg g^-1 d^-1, respectively, with large variations across different habitats and incubation time ( Figure 3 ). During the 56-day incubation period, organic carbon mineralization rates in early stage (days 1 − 7) were relatively higher, and the largest values occurred at day 3. In the middle and late stages (days 7 − 56), the organic carbon mineralization rates decreased with incubation time and tended to be stable ( Figure 3 ). Sediment organic carbon mineralization rates in S. alterniflora habitats (SA-14, SA-10, and SA-6) were larger than those in C. malaccensis habitat (CM), and exhibited an increasing tendency with the invasion degree of S. alterniflora ( Figure 3 ). In addition, organic carbon mineralization rates at the surface (0 − 10 cm) were generally higher than those at subsurface (10 − 20 cm), especially in the early stage of incubation. Seasonally, organic carbon mineralization rates were larger in summer compared to winter in both two sediment layers ( Figure 3 ). During the 56-day incubation, the mean rates of organic carbon mineralization among four habitats under different seasons and depths generally displayed the above-mentioned change characteristics, although some differences did not reach a level of statistical significance ( Figure 4 ).

The cumulative carbon mineralization amounts (C _t) increased rapidly in the early stage of incubation and then gradually tended to be stable ( Figure 5 ). After 56-day incubation, the C _t ranged from 738.47 to 1658.41 μg g^-1, which was highest in SA-14 habitats, followed by SA-10 and SA-6 habitats, and lowest in the CM habitats. Also, the C _t was larger in summer compared to winter, and higher at the surface (0 − 10 cm) compared to the subsurface (10 − 20 cm) ( Figure 5 ). In addition, organic carbon mineralization kinetics were described well by the first-order equation, and the correlation coefficients varied from 0.93 to 0.98 ( Table 2 ). Potential carbon mineralization amounts (C ₀) varied from 695.62 to 1523.28 μg g^-1, which was in the order of SA-10 > SA-10 >SA-6 > CM. The variations in estimated C ₀ among four habitats under different seasons and depths generally were similar to measured cumulative organic carbon mineralization ( Table 2 ). The carbon mineralization rate constant (k) ranged from 0.09 to 0.22. In summer, the k values in S. alterniflora habitats (SA-14, SA-10, and SA-6) were higher than those in C. malaccensis habitat (CM), but with little variation in winter ( Table 2 ).

Sediment TOC contents were significantly related to DOC, EOC, bulk density, TN, NH₄ ⁺, NO₃ ⁻, and NO₂ ⁻ (p< 0.05) ( Table 3 ). The MBC contents in sediment were dramatically associated with DOC, EOC, TN, NH₄ ⁺, and NO₃ ⁻ (p< 0.05). Sediment DOC contents were positively correlated with MBC, EOC, TN, and NO₃ ⁻, but negatively related to bulk density (p< 0.05) ( Table 3 ). Sediment EOC contents were significantly related to TN and inorganic nitrogen (NH₄ ⁺, NO₃ ⁻, and NO₂ ⁻) (p< 0.05), but not associated with other measured geochemical properties (p >0.05). The C _t and C ₀ were significantly correlated with TOC, EOC, temperature, EC, NO₃ ⁻, and NO₂ ⁻ (p< 0.05) ( Table 3 ). Also, the k values were positively related to TOC, EOC, temperature, NO₃ ⁻, and NO₂ ⁻, but negatively associated with pH and EC (p< 0.05). In addition, there are pairwise correlations among the C _t, C ₀, and k values ( Table 3 ).

Exotic plant invasion has obvious effects on sediment geochemical properties and biogenic element contents (Gao et al., 2019; Xia et al., 2021). Our newly revealed results indicate that invasive S. alterniflora changes sediment organic carbon fractions, which improves the understanding of carbon dynamics in intertidal wetlands of estuaries and coasts. In this study, sediment TOC contents were larger in S. alterniflora habitats than in C. malaccensis habitat, and the values increased with the invasion degree of S. alterniflora ( Figure 2 ). Generally, sediment TOC contents in intertidal wetlands of estuaries and coasts are tightly related to vegetation growth, and higher net primary production can increase their contents via roots and litter inputs (Tong et al., 2011; Li et al., 2019; Liu et al., 2021; Zheng et al., 2023). Indeed, invasive S. alterniflora had greater aboveground and root biomass compared to C. malaccensis (Gao et al., 2017), which explained well the aforementioned changes in TOC. Previous studies also found that sediment TOC contents in other intertidal wetlands in China (e.g., Jiaozhou Bay wetlands, Yellow River Estuary wetlands, Yancheng wetlands of Jiangsu, Yangtze Estuary wetlands, and Hangzhou Bay wetlands) were higher in S. alterniflora habitat than in native salt marsh habitats (Zhang et al., 2010; Yang et al., 2013; Zhang et al., 2018; Gao et al., 2019; Liu et al., 2021), demonstrating that S. alterniflora invasion increased organic carbon accumulation in such ecosystems. However, sediment TOC contents in the S. alterniflora habitat in Jiulong River Estuary wetlands and/or Pearl River Estuary wetlands) were lower than those in the mangrove habitat (Yu et al., 2015; Xia et al., 2021), which indicated that S. alterniflora invasion into the mangrove caused organic carbon loss. This phenomenon was mainly attributed to the changes in biomass, and mangroves have larger biomass, leading to a greater accumulation of organic carbon (Yu et al., 2015). In the vertical profile, sediment TOC contents were larger at the surface (0 − 10 cm) than at subsurface (10 − 20 cm) in C. malaccensis habitat, but there were comparable between the two depths in S. alterniflora habitats ( Figure 2 ). Theoretically, sediment TOC contents in the surface layer would be higher compared to the subsurface layer due to the input of aboveground plant litter (Xia et al., 2021). This discrepant result might be attributed to the differences in root systems among these habitats (Emery and Fulweiler, 2014; Jin et al., 2017). Field survey showed that S. alternifolia has more developed root systems compared to C malaccensis, resulting in no significant decrease in TOC contents at the subsurface sediment layer (10 − 20 cm depth) in the former. In general, the root length of S. alternifolia can be more than 1 m, while C malaccensis is about 0.5 m (Liao et al., 2007; Gao et al., 2017). Hence, S. alternifolia invasion altered the vertical distribution characteristics of sediment TOC. Seasonally, sediment TOC contents in these four habitats were larger in summer compared to winter ( Figure 2 ), which might be due to the fact that summer serves as the plant growing season, possessing higher primary productivity (Tong et al., 2011; Gao et al., 2019). Sediment TOC contents continued to increase with invasion chronosequences of S. alterniflora ( Figure 2 ), indicating that sediment carbon accumulation had not yet reached its maximum value at SA-14 habitats, and this finding aligned with the results observed in the Yancheng wetlands of Jiangsu Province and Yellow River Estuary wetlands (Yang et al., 2016b; Zhang et al., 2018). Hence, the changes in sediment TOC contents after S. alterniflora invasion should be further followed up to recognize its carbon storage potential (He et al., 2024).

Sediment labile carbon fractions (e.g., MBC, DOC, and EOC) are sensitive to changes in environmental conditions and have commonly been used as indicators for assessing sediment carbon turnover (Jin et al., 2017; Vidya et al., 2023). In our study, we also discovered that invasive S. alterniflora generally increased sediment MBC, DOC, and EOC contents, although some differences were statistically insignificant ( Figure 2 ). It has been noted that sediment TOC consists of labile and recalcitrant carbon fractions, and the labile carbon fractions are more reflective of the variations in TOC (Song et al., 2012; Fu et al., 2023), resulting in similar change patterns for TOC and their labile fractions. This result was also supported by the positive relationship between measured labile carbon fractions with TOC (p< 0.05, Table 3 ). However, sediment MBC, DOC, and EOC contents across four habitats (SA-14, SA-10, SA-6, and CM) were higher at the surface (0 − 10 cm) compared to the subsurface (10 − 20 cm), which was different from the vertical distribution of TOC in S. alterniflora habitats ( Figure 2 ). This is because the labile fractions are more associated with fresh organic matter, and the availability of plant litter on the surface is generally larger compared to the subsurface (Jin et al., 2017; Xia et al., 2021). Previous works mainly focused on the impact of S. alterniflora invasion on sediment organic carbon contents and stocks in intertidal wetlands, with less research conducted on the changes in its active fractions, and the present study can provide important insight into carbon dynamics in such ecosystems. Compared to carbon contents, the proportions of labile carbon fractions in TOC can better reflect sediment carbon pool turnover (Zhang et al., 2010; Kuzmina et al., 2022). Here, we further calculated the ratios of sediment MBC, DOC, and EOC to TOC. The results showed that MBC/TOC, DOC/TOC, and EOC/TOC values did not differ among four habitats at 0 − 10 cm depth, but these values were lower in S. alterniflora habitats than in C malaccensis habitats at 10 − 20 cm depth, especially in SA-14 ( Figure 6 ). This implied that the changes were less pronounced for carbon turnover rates than carbon contents after S. alterniflora invasion (Jin et al., 2017). Herein, the MBC/TOC ratios are regarded as a microbial quotient (MQ), which characterizes the microbial carbon use efficiency (Cotrufo et al., 2013; Fang et al., 2022). The different change trends in sediment MQ and TOC along invasion chronosequences of S. alterniflora were observed in our study ( Figure 2 , Figure 6 ), which was consistent with previous results that MQ was negatively related to TOC (Yang et al., 2013; Jin et al., 2017).

Sediment organic carbon mineralization means that microorganisms directly use biogenic elements to complete their metabolism, decomposing organic matter and releasing carbon dioxide (CO₂) (Mou et al., 2018; Gaudel et al., 2024). Thus, changes in mineralization characteristics of sediment organic carbon affected by S. alterniflora invasion have the potential to alter organic carbon pools and greenhouse gas emissions in intertidal wetlands of estuaries and coasts (Xia et al., 2021). In this study, sediment organic carbon mineralization rates and cumulative carbon mineralization amounts in S. alterniflora habitats were larger compared to C. malaccensis habitat, and their values increased with S. alterniflora invasion chronosequences, especially at the surface layer in summer ( Figure 3 , 4 , 5 ). Previous studies noted that sediment substrate availabilities were the main factor influencing organic carbon mineralization, and higher substrate contents can stimulate microbial activities and carbon mineralization (Chapman et al., 2019; Tito et al., 2021). Invasive S. alterniflora increased sediment TOC and labile fraction contents ( Figure 2 ), which might be an important reason for the increase in carbon mineralization rates and their cumulative mineralization amounts. This result was also supported by the positive relationship between cumulative carbon mineralization amounts (C _t) with TOC and EOC ( Table 3 ). In addition, our study showed that cumulative carbon mineralization amounts (C _t) were significantly associated with EC, which was similar to the findings of Weston et al. (2011) who noted that salt-water intrusion altered organic carbon dynamics via microbial decomposition. In addition, Yang et al. (2016b) found that invasive S. alterniflora stimulated various microbial groups and microbial respiration, and this is also an important reason for the increase in organic carbon mineralization. Sediment organic carbon mineralization rates and cumulative carbon mineralization amounts across four habitats were significantly higher at the surface layer compared to the subsurface layer ( Figures 3 , 5 ). Sediment TOC contents in C. malaccensis habitat were also larger at the surface than at the subsurface layer, but this was not the case in S. alterniflora habitats ( Figure 2 ). Hence, the vertical distributions of organic carbon mineralization cannot be explained based on changes in TOC contents. Notably, sediment carbon labile fractions (MBC, DOC, and EOC) were larger at the surface than at the subsurface layer ( Figure 2 ). This result implied that sediment organic carbon labile fractions might be the more dominant factor in affecting carbon mineralization dynamics (Mou et al., 2018).

During the 56-day incubation, sediment organic carbon mineralization dynamics were similar across four habitats, and the largest values occurred on day 3 ( Figure 3 ). These changes were tightly associated with the availability of sediment organic carbon. In the early stage (days 1 − 7), sediment carbon labile fractions were rapidly decomposed to provide substrate for microorganisms, which in turn accelerated carbon decomposition and CO₂ release (Mou et al., 2018; Ni et al., 2024). While in the middle and late stages (days 7 − 56), sediment carbon labile fractions decreased, and recalcitrant carbon was not easily utilized by microorganisms, resulting in a decrease in organic carbon mineralization and a tendency toward stabilization (Chapman et al., 2019).

Generally, sediment organic carbon mineralization has obvious seasonal differences. In the present study, the organic carbon mineralization rates and cumulative carbon mineralization amounts were larger in summer compared to winter ( Figures 3 , 5 ), and this was primarily attributed to the temperature changes. Previous studies noted that microbial activities increase with increasing temperature within a certain range (Gao et al., 2018; Kim et al., 2020). In our study area, mean sediment temperatures in winter and summer were 17.28 ± 0.47°C and 32.95 ± 1.09°C, respectively ( Table 1 ), which explained well the aforementioned results.

The mathematical characterization of organic carbon mineralization kinetics in incubation experiments helps to understand the supply and balance ability of organic carbon (Cooper et al., 2011; Luo et al., 2019). The first-order equation in the present study reflected well the organic carbon mineralization kinetics in four different habitats ( Table 2 ). The potential carbon mineralization amounts (C₀) varied from 695.62 to 1523.28 μg g^-1, which was generally higher than the previous findings (Llorente and Turrión, 2010; Mou et al., 2018). The changes in estimated C ₀ in our study were consistent with those of C _t ( Table 2 ), and there was a positive correlation between the two parameters ( Table 3 ), which indicated that sediment carbon decomposition ability was significantly enhanced after S. alterniflora invasion (Lu and Xu, 2014; Rodríguez-Salgado et al., 2017). The carbon mineralization rate constant (k) in S. alterniflora habitats was higher compared to C. malaccensis habitat in summer, further confirming that invasive S. alterniflora raised the effectiveness of organic compounds decomposed by microbial respiration (Mou et al., 2018). Significant relationships were observed between C₀ and k ( Table 3 ), implying that the changes in k values among four habitats might be caused by the carbon pool size (Goberna et al., 2006). Overall, the results indicated that invasive S. alterniflora increased sediment organic carbon contents in estuarine and coastal wetlands, which may be conducive to carbon accumulation and storage (Wang et al., 2023). On the other, organic carbon decomposition and mineralization potential also increased with the invasion degrees of S. alterniflora, and this will accelerate CO₂ emission and subsequently affect climate change (Bu et al., 2015; Gaudel et al., 2024). From this perspective, invasive S. alterniflora does not promote carbon accumulation by reducing carbon decomposition. Hence, the increased release of carbon-containing greenhouse gases caused by S. alterniflora invasion should attract our attention. In recent years, various measures (biological substitution, physical control, or chemical herbicides) were adopted across China to control S. alterniflora expansion (Zheng et al., 2023), which may have substantial importance in mitigating carbon emissions from estuarine and coastal wetlands. However, there are some disputes regarding the eco-environmental significance after the S. alterniflora invasion (Zheng et al., 2023), which certainly looks worthy of further work. In addition, to better understand the responses of carbon dynamics to this invasive S. alterniflora, the ongoing study should also focus on sediment microbial communities related to carbon turnover. Nevertheless, this study provided valuable insight into sediment carbon dynamics and the management of invasive plants in intertidal wetlands of estuaries and coasts.