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Journal of soil science and plant nutrition

versión On-line ISSN 0718-9516

J. Soil Sci. Plant Nutr. vol.16 no.4 Temuco dic. 2016

http://dx.doi.org/10.4067/S0718-95162016005000063 

 

Influence of artificial grassland restoration on soil carbon pool in an arid mining land

 

Yan Mu1,2, Yu Liu2, Fu-Ping Tian3, Xiao-Feng Chang2, Gao-Lin Wu1,2*

 

1College of Landscape Architectural and Arts, Northwest A & F University, Yangling, Shaanxi, 712100, China. *Corresponding author: gaolinwu@gmail.com

2State Key Laboratory of Soil Erosion and Dryland Farming on the Loess Plateau, Institute of Soil and Water Conservation, Chinese Academy of Sciences and Ministry of Water Resources, Yangling, Shaanxi, 712100, China.

3The Lanzhou Scientific Observation and Experiment Field Station of Ministry of Agriculture for Ecological System in the Loess Plateau Area, Lanzhou Institute of Animal and Veterinary Pharmaceutics Sciences, Chinese Academy of Agricultural Sciences, Lanzhou, Gansu, 730050 China.

 


Abstract

Successful reclamation of degraded mine land can contribute to recuperate the vegetation and soil carbon sequestration. In this study, soil carbon pool was assessed in a mining land after short-term reclamation. We measured above- and belowground biomass and soil carbon storage of artificial grassland (Astragalus adsurgens and Medicago sativa), which was established in the reclamation of mining land. The results showed that artificial grassland establishment significantly increased above- and belowground biomass after four-year restoration. Artificial grassland establishment increased soil inorganic and organic carbon content and storage. Soil organic and inorganic carbon content showed a positive increasing along the restoration time. Higher SOC and lower soil bulk density and water content all were attributed to the growth of artificial grassland. These results suggest that establishing artificial grassland with legumes is an effective restoration approach for improving soil carbon pool in the reclaimed mine soils. 

Keywords: Mine land, reclamation, soil carbon, vegetation community

 


 

1. Introduction

Fossil fuel combustion and other anthropogenic activities, have been continually increasing atmospheric greenhouse gas carbon dioxide (CO2) concentrations worldwide, which results in rising global temperatures, hoisting sea levels, and other dangerous effects on the environment (Easterling et al., 2000; Palumbo et al., 2004). Effective managing carbon (C) is the most significant challenge inherent to manage the greenhouse effect (Akala and Lal, 2006). The terrestrial ecosystem plays a major role in moderating the global C cycle, and it is an effective biological scrubber for atmospheric CO2 (Shrestha and Lal, 2006). Enhancing C storage in terrestrial ecosystems is a potential approach to mitigate rising CO2 concentrations (Juwarkar et al., 2010; Palumbo et al., 2004). The biosphere and the pedosphere are the two most important sinks for carbon in the terrestrial ecosystem. The pedosphere, which especially shows potential to sequester C effectively, plays an important role in the overall management of C (Akala and Lal, 2006; Rosenzweig and Hillel, 1999).

Land degradation is caused by various anthropogenic disturbances including mining, which has caused considerable negative impact on terrestrial ecosystems and led to severe soil degradation in many parts of the world (Akala and Lal, 2000). Soil disturbance caused by mining operations where native vegetation and animal communities have been removed and most of the topsoil lost, altered, and buried. Surface mining eliminates vegetation, permanently changes topography, drastically alters soil geological structure, and disrupts hydrologic regimes (Keskin and Makineci, 2009). About 2.88 Mha of land has been destroyed by mining in China (Bai et al., 1999a), the figure is increasing at an alarming rate of 46,700 ha per year (Bai et al., 1999b). Degraded mine lands are often characterized by acidic pH, poor soil structure, low soil fertility, and limited microbial activity (Ussiri et al., 2006). These soils completely regenerated through normal ecological successional processes, but the processes required decades (Juwarkar et al., 2010).

Despite relatively low levels of key nutrients and poor soil structure, degraded mine land shows considerable C sequestration potential (Akala and Lal, 2001). Reclamation of mine land by soil restoration and reestablishment of vegetative cover could lead to successful C sequestration, such as accelerating the natural processes, mitigating negative environmental consequences associated with mining (Akala and Lal, 2000; Yang et al., 2015). Retaining SOC by creating a conducive environment for vegetation regeneration can sequester C and reduce greenhouse effect ultimately. SOC level is an indicator of soil maturity, as well as potential reservoirs for C storage (Rosenzweig and Hillel, 1999; Juwarkar et al., 2010). Depleted SOC pools in reclaimed mine soil ecosystems could be identified according to comparing the SOC level to undisturbed or otherwise similar soils. SOC could be restored through appropriate land use and adoption of scientifically recommended management practices (Guo et al., 2015; Merino et al., 2015; Wu et al., 2016a; 2016b). In order to accurately estimate C storage in soil, both organic and inorganic pools must be considered (Liu et al., 2016). The SIC pool is an important part of the total soil C pool (Hirmas et al., 2010). Soil inorganic carbon (SIC) sequestration is the immobilization of C in the form of pedogenic carbonates, and leaching of carbonates and bicarbonates into the ground water (Akala and Lal, 2006; Tan et al., 2014). The necessary magnitude of SIC exchange in the atmosphere is another very lengthy process, but the formation of secondary carbonate in soil is an effective C sequestration mechanism (Mi et al., 2008). Accumulation of SOC and SIC is a fundamental component of the successful restoration of degraded mine land.

Mining-related SOC depletion trends can be reversed by effective reclamation of mine lands. Reconstructing mine land soil quality requires successfully employing vegetation to improve physical, chemical, and biological soil condition (Bendfeldt et al., 2001). In the present study, abandoned mine land was reclaimed by establishing artificial grasslands to improve the soil organic and inorganic carbon pool. The primary objectives of this paper were to (1) evaluate SOC and SIC stocks as short-term restoration in abandoned mine land; and (2) explore their relation with physical and chemical soil properties in restorated mine land.

2. Materials and Methods

2.1. Study area

The experimental area (39°41,N,110°16,E, altitude, 1413 m a.s. l.) is located at Jungar Banner, Ordos City, China. The study area is a well-known coal mine resource and its land surface was mined extensively and subsequently reclaimed. It belongs to a semi-arid continental temperate monsoon climate. According to the data available for the period 2001-2013 at the study site provided by the National Meteorological Information Center of China, the mean annual air temperature is 7.33 °C. The annual precipitation is 384.75 mm, mainly occurring between July and September (Figure 1). The mean annual evaporation capacity is 1824.7-2896.1 mm, which is approximately three times as much as the mean annual precipitation. Vegetation is dominated by Caragana intermedia Hippophae rhamnoides, Aremsia gmelinii, and Bothriochloa ischaemum. The dominate soil types are aeolian sandy soil and loessial soil, which is infertile and extremely susceptible to erosion.

Figure 1. Annual mean temperature and annual mean precipitation at study site 2001–2013. Note: straight lines in the figure represent the dynamic fitting curve for annual mean temperature and annual mean precipitation changes with time.

2.2. Experimental design

This study compared four different grasslands: 1-year, 2-year, 3-year and 4-year-established artificial grasslands, with Astragalus adsurgens and Medicago sativa on the reclamation land areas and one newly reclaimed land as a control (Figure 2). Each treatment block was about 1 ha and it was comprised by five sampling plots (30 m x 30 m) with random arrangement. Blocks were separated by iron fences . In each of sampling plots of the four grassland types, we established five diagonal sampling quadrants (1.0 m x 1.0 m) to investigate and sample. The growing season is from April to September in study area. The artificial grasslands in our study are excluded from grazing all year.

Figure 2. Four restored grasslands in this study (1-year grassland restoration, R1; 2-year grassland restoration, R2; 3-year grassland restoration, R3; 4-year grassland restoration, R4).

2.3. Soil sampling and determination

Soil samples were taken at five points in each quadrant. Soil sampling was performed with a soil drilling sampler (9 cm inner diameter) in three soil layers, 0–10, 10–20, and 20–30 cm. The same layers were then mixed together to make one sample. All samples were sieved through a 2 mm screen to remove roots and other debris. Soil samples were air-dried and then passed through a 0.14 mm sieve. Soil pH was determined using a soil-water ratio of 1:5, and soil water content before air drying was obtained by the oven-drying method. The soil bulk density (g cm-3) of the different soil layers was measured using the soil cores (volume, 100 cm3) with the volumetric ring method (Wu et al., 2010). Soil organic carbon was assayed by dichromate oxidation (Kalembasa and Jenkinson, 1973). Soil inorganic carbon was measured using the calcimeter method, based on the reaction of SIC with HCl to CO2 (Vuong et al., 2013). Each analysis was completed in three replicates. The following equation was used to calculate soil organic carbon storage (SOS) (Deng et al., 2013):

SOS= BD X SOC X D /10

in which SOS is soil organic carbon storage (Mg ha-1), BD is soil bulk density (g m-3), SOC is soil organic carbon concentration (g kg-1), and D is soil thickness (cm).

2.4. Plant sampling

In each quadrant, aboveground plant parts were cut, collected, and put into envelopes and tagged in early September. To measure belowground biomass, soil sampling was done three times in three soil layers, 0–10, 10–20, and 20–30 cm at a depth of 0–30 cm in each quadrant using a 9 cm-diameter root auger. The majority of the roots were found in the soil samples as-obtained and isolated using a 0.5 mm sieve. This process likely failed to distinguish all dead root tissue, so thus is referred to as standing root mass measurement. The root tissue and aboveground plant were dried at 80 ¡ãC for 48 h and weighed to determine the dry biomass.

2.5. Statistical analyses

All data were expressed as mean ± standard error (SE). One-way ANOVA analyses were conducted to identify the effects of establishment time of artificial grassland on aboveground/belowground biomass, SIS, SOS, SIC, and SOC. Post hoc comparisons were made using Tukey,s honest significant difference (HSD). Significant differences were evaluated at the 0.05 level. Pearson Correlation analyses were used to test the relationships between soil and plant factors. Regression parameters and figures were calculated by Sigmaplot Version 12.5 (Systat Software Inc., San Jose, CA, USA) and statistical tests were carried out using SPSS Version 17.0 (SPSS, Chicago, IL, USA).

3. Results

3.1. Plant community response and soil properties

Artificial grassland establishment significantly increased aboveground biomass after three years of restoration (p<0.05) from R1 (64.14 ± 11.47 g m-2) to R4 (525.09 ± 96.47 g m-2), and also significantly increased the belowground biomass after four years of restoration (p<0.05; Figure 3) from R3 (225.88 ± 8.92 g m-2) to R4 (770.31 ± 172.37 g m-2) at 0-30 cm depth. As for soil properties among R1, R2, R3, and R4 grasslands, artificial grassland establishment decreased soil bulk density (Figure 4a) and soil water content (Figure 4b), but there were no significant effects caused by number of restoration years or soil depths on soil bulk density or soil water content.

Figure 3. Changes in aboveground biomass (AGB) and belowground biomass (BGB) within three soil depths for 1-, 2-, 3-, and 4-year (R1, R2, R3, R4) artificial grasslands. Significant differences in AGB and BGB between different restoration times are indicated by asterisks at p<0.05.

Figure 4. Changes in soil water content (b) and soil bulk density (a) within three soil depths for newly reclaimed land (CK) and 1-, 2-, 3-, and 4-year (R1, R2, R3, R4) artificial grasslands. The different letters represent the significant differences at p<0.05.

3.2. Soil carbon content response and storage

There was a positive effect of soil inorganic and organic carbon content on artificial grassland. Establishing artificial grassland increased both soil inorganic and organic carbon content (Figure 5). R2 showed the highest inorganic carbon content (Figure 5a) and R1 showed the highest organic carbon content (Figure 5b) in the study period. Soil organic carbon content increased from 0.58 ± 0.07 g kg-1 to 0.92 ± 0.06 g kg-1, and soil inorganic carbon content increased from 3.55 ± 0.14 g kg-1 to 7.78 ± 0.23 g kg-1 at the 0-30 cm depth over 4 years. Restoration time had no significant impact on soil inorganic/organic carbon content.

Figure 5. Changes in soil inorganic carbon (SIC) content (a) and soil organic carbon (SOC) content (b) within three soil depths for newly reclaimed land (CK) and 1-, 2-, 3-, and 4-year (R1, R2, R3, R4) artificial grasslands.

Similar trends were observed for soil inorganic and organic carbon storage; establishing artificial grassland increased soil inorganic and organic carbon storage. The soil inorganic carbon storage in R2 was higher than CK, R1, R3, and R4 grasslands (Figure 6a). Soil organic carbon storage in R1 was found the higher than the other grasslands (Figure 6b). Soil organic carbon storage in the artificial grassland increased from 17.58 ± 3.14 Mg ha-1 to 35.27 ± 14.62 Mg ha-1, and soil inorganic carbon storage increased from 2.85 ± 0.52 Mg ha-1 to 4.26 ± 0.18 Mg ha-1 at 0-30 cm depth.

Figure 6. Changes in soil inorganic carbon (SIC) storage (a) and soil organic carbon (SOC) storage (b) within three soil depths for newly reclaimed land (CK) and 1-, 2-, 3-, and 4-year (R1, R2, R3, R4) artificial grasslands.

3.3. Relationship between community and soil properties

Correlation analyses showed that the restoration time significantly positively related to community coverage (R=0.883, p<0.01) and aboveground biomass (R=0.734, p<0.01), and significantly negatively related to soil water content (R= -0.6874, p<0.01; Table 1). Community coverage significantly negatively related to plant height (R= -0.492, p<0.05) and positively related to aboveground biomass (R=0.679, p<0.01). Soil water content and bulk density showed a significant positive correlation (R=0.605, p<0.05; Table 1). Soil organic and inorganic carbon content showed a positive correlation with short–term restoration, but the relation was not significant (p>0.05, Table 1).

Table 1. Pearson correlation coefficients between bulk density (BD), soil water content (SWC), coverage, height, belowground biomass (BGB), aboveground biomass (AGB), soil organic carbon content (SOC), and soil inorganic carbon content (SIC).

Note: * P<0.05; ** P < 0.01.

4. Discussion

Rebuilding Astragalus adsurgens and Medicago sativa grasslands artificially is vital for successful restoration of vegetation productivity at abandoned mine lands. 3-year grassland restoration showed significantly more aboveground biomass than 1 and 2-year grassland restoration. There were distinct reductions in soil bulk density and soil water content after mine land reclamation. This result is consistent with the results found by Zhao et al. (2013), who observed that reclamation significantly decreased the bulk density of mined soil. Alfalfa (Medicago sativa) has been proven as one of the productive forage crops, and also is one of the effective artificial vegetation materials to conserve soil (Zhao et al., 2004). Alfalfa depleted so much soil water through evapotranspiration and resulted in a distinctive and persistent dry layer (with soil water content close to wilting points) at its root depth (Al-Rumikhani, 2002; Wang et al., 2010).

The accumulation of SOC in mining soils has been previously recognized as the key factor in activation of soil biological processes and nutrient maintenance (Lorenz and Lal, 2007). SOC is typically deficient in mine soil, which limits long-term vegetation establishment for restoration of degraded grassland. Factors that affected C storage and protection in reclaimed mine soil include microbial activity, nutrient availability, soil aggregation, C build-up, and soil profile. Establishing grassland in mine land can increased soil inorganic and organic carbon storages. This phenomenon is possibly dependent on aboveground biomass growth and input, and increased capacity of the mine lands to sequester C. Legumes derived N is qualitatively important for building up soil organic matter and carbon storage (Wu et al., 2016a).

Successfully utilizing vegetation for C sequestration may require extensive and long-term effort. During initial stages of reclamation, legumes show a great deal of potential in sequestrated carbon. Legumes added N to the soil, which in turn enhances soil N supply rates and sustains plant growth in a positive feedback loop (Wu et al., 2016a). The increasing biomass and litter can provide more organic matter inputs, which increased the relative decomposition rates of SOC. The plant needed to deplete some SOC to sustain growth as restoration time increase, but parts of the plant tissues that fell and then created soil organic matter input to help maintain a high level of SOC effectively in the top soil (0-10 cm). The accumulation of organic matter was previously recognized as the primary mechanism in the activation of soil biological processes (Sourkova et al., 2005; Frouz et al., 2007). The development of these active microbial populations had a direct impact on the activation of vital organic compound transformation processes, and release of inorganic forms of nitrogen and phosphorus that are directly available to growing plants (Heras, 2009).

SIC exists largely in the form of pedogenic calcite, which is present in semi-arid and arid regions in the form of calcareous, calcic, and petrocalcic horizons (Hirmas et al., 2010). Thus, SIC sequestration is likely the most significant pathway of C sequestration in arid and semi-arid regions. Our study showed that reclamation of mine lands increases SIC content and storage, the highest values of which are 1.03 ± 0.07 g kg-1 and 4.26 ± 0.18 Mg ha-1, respectively. The decomposition rate of plant residues is about 80-90% in the arid area of northwest China, and the mineralization rate is 5-10 times that of wet soil (Deng et al., 2013). A large portion of the carbonate parent material, as well as the calcium accumulation, increased the proportion of SIC in the research area. The CO2 partial pressure in the soil and soil moisture increased during the high temperature and rainy summer. As soil water and CO2 partial pressure changed, the CO2 produced by SOC decomposition converted to carbonate C by precipitation, formulating a SOC-CO2-SIC micro carbon cycle system in the soil. So, the ploughing process to establish artificial grassland and then vegetation restoration all could affect the SIC storage, because a change of one of the soil moisture, pH, CO2 partial pressure, and Ca2+ and HCO3- concentrations would cause an effect on SIC (Liu et al., 2016).

5. Conclusions

Artificial grassland establishment significantly increased above- and belowground biomass after four-year restoration. Artificial grassland establishment increased soil inorganic and organic carbon content and soil carbon storage. Soil organic/inorganic carbon content showed a positive correlation with short–term restoration, and higher SOC and lower soil bulk density/water content were attributed to artificial grassland growth. The results of this study altogether suggest that establishing artificial grassland by Legumes is an effective restoration approach for improving soil carbon in reclaimed mine soils.

Acknowledgment

This research was funded by the Project of Natural Science Foundation of China (NSFC41401613, 31372368, 41303062), the "Light of West China" Program of CAS (XAB2015A04), the Action Plan for West Development Project of Chinese Academy of Sciences (KZCX2-XB3-13). The authors thank Dr. Jason Qi for the language revision of this manuscript.

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