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Spatial variability of soil carbon, nitrogen, and phosphorus content and storage in an alpine wetland in the Qinghai-Tibet Plateau, China.


Wetland is an important component of the terrestrial ecosystem, and plays a crucial role in modifying regional climate, protecting biodiversity, and sequestrating carbon (C), nitrogen (N), and phosphorous (P) (Howarth et al. 1996; Mitsch and Gosselink 2000). Increasing interest has been focused on the role of freshwater wetlands, particularly northem peatlands, as C sinks (White and Reddy 2000; Clair et al. 2002; Chmura et al. 2003), because these wetlands store about one-third of the global terrestrial soil organic C (SOC) of 1395 Gt (Post et al. 1982). Changes in N and P in wetland ecosystems have also received attention, since they are important nutrients for plant growth (Mitsch and Gosselink 2000). However, few studies have been carried out on changes in SOC, N, and P storage in the alpine wetland ecosystems in the Qinghai-Tibet plateau in China, despite their important effects on global changes (Gao 2006) and wetland productivity (Mitsch and Gosselink 2000; Bai et al. 2005).

Physical and chemical properties of soils vary spatially due to the nature of soil parent material and soil position in the landscape (Riha et al. 1986) and water table fluctuations (Johnston et al. 2001). When a soil shifts from saturated to unsaturated conditions, oxidative reactions will be enhanced, resulting in increased soil C[O.sub.2] emission and decreased [N.sub.2]O or C[H.sub.4] emissions (Li et al. 2004). Lal (2004) suggested that land-use changes (i.e. conversion of natural to agricultural or pasture ecosystems, drainage of wetlands) are among major factors affecting greenhouse gases emissions. It has become clearer that C and N storage in wetlands shows a significant decrease due to the conversion of wetlands to agricultural ecosystems (Lal 2004; Wang et al. 2004, 2006; Zhang et al. 2008), but that storage will increase with increasing time after abandonment of cultivated wetland (Zhang et al. 2007). Additionally, different landscape, land-use (soil management), and hydrological patterns might affect N (Bai et al. 2007) and P transfers and forms (Tiessen 1995), which can affect water quality of adjacent rivers or lakes (Mitsch and Gosselink 2000; Bai et al. 2007) and possible successional changes (Prusty et al. 2009).

Generally, human activity has adversely affected global C, N, and P cycles, and contributed to an alteration of climate that will generate discernible feedbacks to all organisms and ecosystems on the Earth (Mitsch and Gosselink 2000; Wang et al. 2006; He et al. 2008). Therefore, understanding the store and storage potential of C, N, and P helps us understand how ecosystems would respond to natural and anthropogenic disturbances under different management strategies (He et al. 2008). As a result of economic development and population growth, many alpine wetlands were drained and converted to pasture in the Zoige Plateau of China in the late 1970s. The rapid expansion of livestock numbers and drainage of wetlands have caused significant degradation or desertification of alpine wetlands (Bai et al. 2008), accelerating peat decomposition and carbon loss, and sharp decline of wetland biodiversity (Bai et al. 2008), despite some measures (e.g. building natural reserves, banning pasture) to restore and protect these alpine wetlands in the past. However, little information is available on spatial variability of C, N, and P in the alpine wetlands after long-term drainage in this region. Therefore, the primary objectives of this work are: (1) to study the spatial variability of SOC, N, and P storage in a drained alpine peatland; and (2) to reveal the possible relationship between them and other soil properties.


Materials and methods

Study area

The study area is in Hongyuan county in the Zoige plateau, south-east of the Qinghai-Tibet plateau of China (see Fig. 1), 33[degrees]10'-34[degrees]06'N, 101[degrees]36'-103[degrees]25'E. Peat soils and alpine meadow soils are widely developed in this region. The Zoige plateau wetland has an important ecological function for retaining water on the upper reach of the Yellow River. This region has a continental humid and semi-humid monsoon climate for an alpine temperature zone, and it is one of the abundant precipitation zones in the Yellow River basin, with annual mean precipitation of 600-800 mm. The dominant plant cover is Carex muliensis community. Hundreds of ditches (~1 m width) have been built in this region since 1970s for drainage of wetlands and grazing. Due to long-term drainage, serious degradation has occurred in these alpine wetlands and Cremanthodium lineare has encroached into the Carex marsh (Fig. 1).

Soil sampling and analysis

A sampling plot near a ditch (built in 1970s) was selected in Hongyuan county. A 55 by 55 m sampling grid (0.3025 ha) was established as the sampling area. Grid points (i.e. sampling points) were spaced evenly 1 m apart, and 66 grid points were randomly selected. Soil samples were collected from the upper 0.3 m in June 2004. A single 48-mm-diameter soil core was collected from the 0-0.3 m depth within a 0.20-m radius surrounding each grid point, oven-dried at 70[degrees]C for 48h, and weighed for bulk density and moisture content determination. Three 20-mm-diameter soil cores were collected from the 0-0.3 m depth within a 0.20-m radius surrounding each grid point and mixed to form a composite sample. Soil samples were placed in polyethylene bags and brought back to the laboratory. All samples were air-dried at room temperature and sieved through a 2-mm nylon sieve to remove coarse debris and stone. The air-dried soils were then ground with a pestle and mortar for soil chemical analysis. Soil physical and chemical properties are listed in Table 1.

Soil organic matter was determined by the method of Walkley and Black (1934). Soil organic matter was converted to SOC by the Bemmelen index (0.58) because the determination was done by conventional wet combustion with [Cr.sub.2][[O.sub.7.sup.2-] (Wen 1984). Total N (TN) was determined by a modified micro-Kjeldahl digestion procedure. Total phosphorus (TP) was extracted from soils with 1N HCI after ignition at 550[degrees]C (Aspila et al. 1976). Soil pH([H.sub.2]O) was measured using a pH meter (soil : water 1 : 5). For quality assurance and quality control throughout the experiments and analyses, all the extracting reagents were prepared using metal-free, AnalaR-grade chemicals. Double-distilled water prepared using quartz double-distillation assembly was used for preparing the reagents (Prusty et al. 2009). All the digestion was conducted in duplicate and each batch included blanks to validate the digestion operation.

We calculated the SOC density (SOCD, kg C/[m.sup.2]), soil total N density (STND, kg N/[m.sup.2]), and soil total P density (STPD, kg P/[m.sup.2]) on a ground-area basis up to 0.3 m depth as follows:

SOCD = H x [rho] x SOC x (1 - [[delta].sub.2]mm/100) x [10.sup.-1]

STND = H x p x TN x ([1-[[delta].sub.2]mm/100) x [10.sup.-1]

STPD = H x [rho] x TP x (1 - [[delta].sup.2]mm/100) x [10.sup.-1]

where H, [rho], and [[delta].sub.2] mm are the soil thickness (cm), bulk density (g/[cm.sub.3]), and volumetric percentage, respectively, of the fraction >2mm (rock fragments); SOC, TN, and TP are contents in mg/kg.

Statistics analysis and mapping

Geostatistical analysis was conducted using GS+ for windows (version 5.1, Gamma Design Softeare, Plainwell, MI). Only isotropic semivariograms were considered, and semivariance parameters for spherical or exponential models are reported for SOCD, STND, and STPD; and spatial distribution of SOCD, STND, STPD, and soil moisture using Surfer 7.0 (Golden Software, Inc., Golden, CO). Point kriging with no search radius was used as an unbiased, weighted, linear interpolation method that minimises total parameter variance by incorporating semivariogram functions to create contour maps (Isaaks and Srivastava 1989). In addition, Pearson analysis was performed using the SPSS 10.0 statistical package to examine the possible relationship between selected soil properties.

Results and discussion

Mean contents of C, N, and P in drained peat soils

Mean SOC contents were 35.81 [+ or -] 3.24% in the drained peat soils (Table 1), which was ~2 times the SOC content in flooded peat soils in this region (Gao 2006). This was in agreement with the findings of Tong et al. (2005) and Gao (2006) that higher SOC contents occurred in peat soils with lower water contents (<70%) than with higher water contents. This indicates that drainage led to an increase in SOC contents in surface peat soils with certain water contents compared with flooded soils. However, Li et al. (2004) reported that when wetland soils shifted from saturated to unsaturated conditions, the oxidative reactions enhanced SOC loss by C[O.sub.2] emission. This was probably related to the fact that peat soils are dominated by incompletely decomposed plant debits or dead roots compared with other wetland soils, and wet conditions with good accretion (e.g. water content 78.60%, elevated bulk density 0.58 [+ or -] 0.22 g/[cm.sup.3]; Table 1) could greatly contribute to their decomposition and returning nutrients to soils.

Mean TN content in the drained peat soils was 2.35 [+ or -] 0.27%, which was ~4 times higher than in the flooded peat soils in this region (Gao 2006). This could be explained by the fact that drainage or aeration of wetland soils would increase N mineralisation and inorganic-N contents (Olde Venterink et al. 2002). Also, the low C/N ratios in these soils (>20, Table 1) contributed to N mineralisation. Hefting et al. (2004) also found the end product of N mineralisation was nitrate under low water table levels (<-0.30 m), while N loss could only occur by denitrification and leaching due to rainfall events under the above conditions. Bai et al. (2005) stated that water table fluctuations in floodplain wetlands could affect nitrogen transformation and mobility.

With respect to soil P, the mean content (996.35 mg/kg) in drained wetland soils with a narrow soil pH range 5 6 was also higher than in the original wetland soils of this region (741.10mg/kg; He and Zhao 1999). Richardson (1985) stated that drainage of wet soils decreased plant P availability by Fe-P complexation, particularly in the pH range 4-6. Kang and Freeman (1999) also suggested that water tables might be the dominant controlling factor to regulate the inorganic P concentrations.

Spatial variability of SOCD, STND, and STPD in the drained alpine wetland

Incorporation of bulk density into the value of areal storage results gives a more accurate description of the total mass of soil nutrients within a given area (DeBusk et al. 1994), since soil roots occupy a volume of soil rather than a mass of soil (Johnston et al. 2001). A summary of mean C, N, and P concentrations on the basis of volumetric units in top 0.3 m of peat soils is shown in Table 2. The mean C, N, and P storages were nearly 1 order of magnitude higher in the peat soils studied here than in peat soils of a northern Everglades marsh reported by DeBusk et al. (1994). The spatial variations of SOCD, STND, and STPD were large, with the coefficients of variation (CV) of >30% (Table 2). Although the CV is an index of the overall variation or heterogeneity of a given variable, the statistical analyses could not discern quantitative changes in spatial patterns (Brye et al. 2004). Therefore, the spatial variations of SOCD, STND, and STPD were assessed using geostatistical analysis and kriging techniques.

The range parameters from spherical and exponential semivariogram models for SOCD, STND, and STPD were <4 m, suggesting spatial dependence among sampling points at 1-m spacing and that data were truly independent within the sampling area (Table 3). A spherical model best characterised the structure of the semivariograms for SOCD and STPD, and an exponential model for STND. Similarly, these models for SOCD, STND, and STPD had small positive nuggets, indicating a positive nugget effect, a sampling error, and/or random and inherent variability of SOCD, STND, or STPD (Liu et al. 2006). Generally, the nugget-to-sill ratio ([C.sub.0]/[C.sub.0]+C) can be used to classify the spatial autocorrelation of soil properties. A variable would be considered to have a strong spatial dependence if the ratio is [less than or equal to] 25%, and have a moderate spatial dependence if the ratio is 25-75%; otherwise, the variable has a weak spatial autocorrelation (Cambardella et al. 1994). In this study, the nugget-to-sill ratios showed strong spatial dependence for SOCD, STND, and STPD ([C.sub.0]/[C.sub.0]+C <0.03; Table 3), which might be mainly attributed to the effects of drainage of wetlands. Also, the spatial component (C/[C.sub.0]+C) in the data nearly completely explained the total variability in SOCD, STND, and STPD. Higher spatial variability could also be observed for SOCD, STND, and STPD in top 0.30 m soils in Fig. 2. Additionally, similar spatial distributions with these patches of lower or higher C, N, and P storage were observed (Fig. 2). Correlation analysis also showed there were significant correlations between SOCD, STND, and STPD (P<0.01; Table 4). Similar trends of enrichment at the eastern part (far from the drained ditch) and upper left comer (near the drained ditch) were observed within this study area. Results showed steep gradients of SOCD, STND, and STPD in the central and south parts along the casting direction.


Effects of selected soil properties on C, N, and P storage in the drained alpine wetland

As shown in Figs 2 and 3, the changing trends of SOCD, STND, and STPD were opposite to that of soil moisture, i.e. those patches with higher C, N, and P storage had lower soil moisture. Correlation analysis also showed that SOCD, STND, and STPD were significantly and negatively correlated with soil moisture (P<0.01), while positively correlated with bulk density (P<0.01) (Table 4), which indicated that C, N, and P storage in top 0.30m soils was lower under unsaturated conditions with higher soil moisture (>70%) due to lower bulk density. However, higher spatial variations of SOCD, STND, STPD, and bulk density were consistently observed in this region (Tables 1 and 2). This was probably related to wetland drainage, since drainage would decrease soil moisture contents and elevate bulk density of soils due to soil compaction. Minkkinen and Laine (1998) also showed the peat layer was decreased by 0.22m after 60 years of drainage in Finland peatlands. Gao (2006) also reported that the sedimentation rates of peat showed a decrease, from 0.036 g/[cm.sup.2].year in 1930s (before drainage) to 0.021g/[cm.sup.2].year in 1980s (after drainage) in this region. Therefore, higher SOCD, STND, and STPD in top 0.30m soils of drained alpine wetland compared with flooded alpine wetland did not indicate an increase in C, N, and P storage in whole peat layers after drainage. On the contrary, drainage might decrease the total storage of C, N, and P in whole peat layers in this region due to SOM decomposition in surface soils (Gao 2006; Bai et al. 2009). Frolking et al. (2001) also reported that soil moisture was the important factor influencing the balance of the decomposition and accumulation of SOM. Therefore, the elevated bulk density due to drainage could significantly impact C, N, and P storage on a volumetric basis. No significant relationship was observed between C, N, and P contents and soil moisture, despite significant correlations being reported by Tong et al. (2005) and Gao (2006) in peat soils and by Bai et al. (2005) in marsh soils. Although linear or exponential increase in SOC contents with increasing bulk density was reported by Wu et al. (2003), a weak negative correlation was observed between SOC and BD in this study. There were significant correlations between TND and TN and C/N ratios. STPD was positively correlated with TP (P < 0.01). However, no significant correlations was observed between pH and any of SOCD, STND, or STPD, despite soil pH values being negatively correlated with SOC (P<0.05) and TP (P<0.01) (Table 4).



Higher C, N, and P contents or storage in top 0.30 m peat soils can be observed after drainage. This suggested that water table fluctuation will result in an increase in uncertainty and instability of C sequestration in peatlands based on 0.30 m and 1 m depth soil profiles (Song et al. 2005; He et al. 2008), since there is lower C, N, and P storage at the same soil depths in flooded peatland than drained peatlands. Moreover, there is higher spatial variability at field sampling scale. Spherical models for SOCD and STPD and an exponential model for STND best characterised the structure of their semivariograms.

Therefore, it is necessary to classify peatlands into such subcategories as flooded, seasonally flooded, and non-flooded and to sample intensively for precisely estimating C storage at regional or global scales. Soil fertility assessment and wetland management also require finer detail and greater certainty about soil spatial variability through on-site, intensive sampling than is provided by soil surveys (Gaston et al. 2001 ; Bai et al. 2005).

The uncertainty of estimating C, N, and P storage will be greatly reduced as result of incorporating the whole thickness of peat layers developed on the parent materials. Additionally, drainage of wetlands will increase the potential emission of CO2 due to SOM decomposition. Some steps have been taken to restore hydrological conditions in these drained alpine wetlands in the Zoige plateau; this will reduce potential C loss and help to alleviate global warming.

DOI: 10.1071/SR09171


The research was supported by the National Basic Research Program of China (Grant Nos 2010CB951102 and 2006CB403301), the National Natural Science Foundation (Nos 50879005, U0833002, 40701003, and 30700108) and the Emphasis Project Fund of National Eleven Five-Year Scientific and Technical Support Plans (No. 2006BAB04A08). We express our thanks to the members of the project who provided invaluable support during the course of collecting soil samples and chemical analysis of the soil samples. We are also grateful to the centre analysis of Beijing Normal University.


Aspila KI, Agemian H, Chau ASY (1976) A semi-automated method for the determination of inorganic, organic and total phosphate in sediments. Analyst 101, 187-197. doi: 10.1039/an9760100187

Bai J, Cui B, Yang Z, Xu X, Ding Q, Gao H (2009) Heavy metal contamination of cultivated wetland soils along a typical plateau lake from southwest China. Environmental Earth Science doi: 10.1007/ s 12665-009-0160-z

Bai J, Deng W, Wang Q, Ding Q, Gao H (2007) Spatial distribution of inorganic nitrogen contents of marsh soils in a fiver floodplain with different flood frequencies from Soil-Defrozen Period. Environmental Monitoring and Assessment 134, 421-428. doi: 10.1007/s 10661-0079633-2

Bai J, Ouyang H, Cui B, Wang Q, Chen H (2008) Changes in landscape pattern of alpine wetlands on the Zoige Plateau in the past four decades. Acta Ecologica Sinica 28(5), 2245-2252. doi: 10.1016/S1872-2032(08) 60046-3

Bai J, Ouyang H, Deng W, Zhu Y, Zhang X, Wang Q (2005) Spatial distribution characteristics of organic matter and total nitrogen of marsh soils in fiver marginal wetlands. Geoderma 124(1-2), 181-192. doi: 10.10016/j.geoderma.2004.04.012

Brye KR, Slaton NA, Mozaffari M, Savin MC, Norman RJ, Miller DM (2004) Short-term effect of land leveling on soil chemical properties and their relationships with microbial biomass. Soil Science Society of America Journal 68, 924-934. doi: 10.2136/sssaj2004.0924

Cambardella CA, Moorman TB, Novak JM, Parkin TB, Karlen DL, Turco RF, Konopka AE (1994) Field-scale variability of soil properties in Central Iowa soils. Soil Science Society of America Journal 58, 1501 1511. doi: 10.2136/sssaj1994.03615995005800050033x

Chmura GL, Anisfeld SC, Cahoon DR, Lynch JC (2003) Global carbon sequestration in tidal, saline wetland soils. Global Biogeochemical Cycles 17(4), 1111. doi: 10.1029/2002GB001917

Clair TA, Arp P, Moore TR, Dalva M, Meng FR (2002) Gaseous carbon dioxide and methane, as well as dissolved organic carbon losses from a small temperate wetland under a changing climate. Environmental Pollution 116, S143 S148. doi: 10.1016/S0269-7491(01)00267-6

DeBusk WF, Reddy KR, Koch MS, Wang Y (1994) Spatial distribution of soil nutrients in a northern Everglades marsh: water conservation area 2A. Soil Science Society of America Journal 58(2), 543-552. doi: 10.2136/sssaj 1994.03615995005800020042x

Frolking S, Roulet NT, Moore TR, Richard PJH, Lavoie M, Muller SD (2001) Modelling northern peatland decomposition and peat accumulation. Ecosystems 4, 479-498. doi: 10.1007/s10021-001-0105-1

Gao JQ (2006) The carbon accumulation and its response to climate change in Zoige wetland ecosystem of Qinghai Tibet plateau. PhD Dissertation, The institute of Geographical Sciences and Natural Resources Research, Chinese Academy of Sciences. China.

Gaston LA, Locke MA, Zablotowicz RM, Reddy KN (2001) Spatial variability of soil properties and weed populations in the Mississippi Delta. Soil Science Society of America Journal 65, 449-459. doi: 10.2136/sssaj2001.652449x

He C, Zhao Q (1999) The conservation of wetlands biodiversities and their sustainable utilization in Zoige plateau. Journal of Natural Resources 14(3), 238 244. [in Chinese]

He N, Yu Q, Wu L, Wang Y, Han X (2008) Carbon and nitrogen store and storage potential as affected by land-use in a Leymus chinensis grassland of northern China. Soil Biology & Biochemistry 40, 2952-2959. doi: 10.1016/j.soilbio.2008.08.018

Hefting M, Clement JC, Dowriek D, Cosandey AC, Bemal S, Cimpian C, Tatur A, Burt TP, Pinay G (2004) Water table elevation controls on soil nitrogen cycling in riparian wetlands along a European climatic gradient. Biogeochemistry 67, 113-134. doi: 10.1023/B: BIOG.00000 15320.69868.33

Howarth RW, Billen G, Swaney D (1996) Regional nitrogen budgets and riverine N and P fluxes for the drainages to the North Atlantic ocean: natural and human influences. Biogeoehemistry 35, 75-139. doi: 10.1007/BF02179825

Isaaks EH, Srivastava RM (1989) 'An introduction to applied geostatistics.' (Oxford University Press: New York)

Johnston CA, Bridgham SD, Schubauer-Berigan JP (2001) Nutrient dynamics in relation to geomorphology of riverine wetlands. Soil Science Society of America Journal 65(2), 557 577. doi: 10.2136/ sssaj2001.652557x

Kang H, Freeman C (1999) Phosphatase and arylsulphatase activities in wetland soils: annual variation and controlling factors. Soil Biology & Biochemistry 31 (3), 449-454. doi: 10.1016/S0038-0717(98) 00150-3

Lal R (2004) Soil carbon sequestration impacts on global climate change and food security. Science 304, 1623-1627. doi: 10.1126/science.1097396

Li C, Cui J, Sun G, Trettin C (2004) Modelling impacts of management on carbon sequestration and trace gas emissions in forested wetland ecosystems. Environmental Management 33(Suppl. 1), S176-S186. doi: 10.1007/s00267-003-9128-z

Liu D, Wang Z, Zhang B, Song K, Li X, Li J, Li F, Duan H (2006) Spatial distribution of soil organic carbon and analysis of related factors in croplands of the black soil region, Northeast China. Agriculture, Ecosystems & Environment 113, 73-81. doi: 10.1016/j.agee.2005.09.006

Minkkinen K, Laine J (1998) Long-term effect of forest drainage on the peat carbon stores of pine mires in Finland. Canadian Journal of Forest Research 28, 1267-1275. doi: 10.1139/cjfr-28-9-1267

Mitsch WJ, Gosselink JG (2000) 'Wetlands.' (Van Nostrand Reinhold: New York)

Olde Venterink H, Davidsson TE, Kiehl K, Leonardson L (2002) Impact of drying and re-wetting on N, P and K dynamics in a wetland soil. Plant and Soil 243, 119-130. doi: 10.1023/A: 1019993510737

Post WM, Emanuel WR, Zinke PJ, Stangenberger AG (1982) Soil carbon pools and world life zones. Nature 298, 156-159. doi: 10.1038/298156a0

Prusty BAK, Chandra R, Azeez PA (2009) Distribution of carbon, nitrogen, phosphorous and sulfur in the soil in a multiple habitat system in India. Australian Journal of Soil Research 47, 177-189. doi: 10.1071/S R08087

Richardson CJ (1985) Mechanisms controlling phosphorous retention capacity in freshwater wetlands. Science 228, 1424-1427. doi: 10.1126/ science.228.4706.1424

Riha SJ, James BR, Senesac GP, Pallant E (1986) Spatial variability of soil pH and organic matter in forest plantations. Soil Seience Society of America Journal 50(5), 1347-1352. doi: 10.2136/sssaj1986.03615995 005000050053x

Song G, Li L, Pan G, Zhang Q (2005) Topsoil organic carbon storage of China and its loss by cultivation. Biogeochemistry 74, 47-62. doi: 10.1007/s 10533-004-2222-3

Tiessen H (1995) 'Phosphorus in the global environment--transfers, cycles and management.' SCOPE 54. (John Wiley and Sons: New York)

Tong CL, Zhang W J, Wang HQ, Tang GY, Yang GR, Wu JS (2005) Relationship between organic carbon and water content in four type wetland sediments in Sanjiang Plain. Chinese Journal of Environmental Science 26(6), 38-42.

Walkley A, Black IA (1934) An examination of the Degtjareff method for determining soil organic matter and a proposed modification of the chromic acid titration method. Soil Science 37, 29-38. doi: 10.1097/ 00010694-193401000-00003

Wang G, Ma H, Qian J, Chang J (2004) Impact of land use changes on soil carbon, nitrogen and phosphorous and water pollution in an arid region of northwest China. Soil Use and Management 20, 32-39. doi: 10.1079/ SUM2 003220

Wang GP, Liu JS, Wang JD, Yu JB (2006) Soil phosphorous forms and their variations in depressional and riparian freshwater wetlands (Sanjiang Plain, Northeast China). Geoderma 132, 59-74. doi: 10.1016/ j.geoderma.2005.04.021

Wen QX (1984) 'Study methods of soil organic matter.' (Agriculture Press: Beijing) [in Chinese]

White JR, Reddy KR (2000) Influence of phosphorous loading on organic nitrogen mineralization of Everglades soils. Soil Science Society of America Journal 64, 1525 1534. doi: 10.2136/sssaj2000.6441525x

Wu H, Guo Z, Peng C (2003) Land use induced changes of organic carbon storage in soils of China. Global Change Biology 9, 305-315. doi: 10.1046/j.1365-2486.2003.00590.x

Zhang JB, Song CC, Wang SM (2007) Dynamics ofsoil organic carbon and its fractions after abandonment ofcultivated wetlands in northeast China. Soil & Tillage Research 96, 350-360. doi: 10.1016/j.still.2007.08.006

Zhang JB, Song CC, Wang SM (2008) Short-term dynamics of carbon and nitrogen after tillage in a freshwater marsh of northeast China. Soil & Tillage Research 99, 149 157. doi: 10.1016/j.still.2008.01.010

Manuscript received 30 September 2009, accepted 3 May 2010

Junhong Bai (A,D), Hua Ouyang (B), Rong Xiao (A), Junqin Gao (C), Haifeng Gao (A), Baoshan Cui (A), and Laibin Huang (A)

(A) State Key Lab of Water Environment Simulation, School of Environment, Beijing Normal University, Beijing 100875, P.R. China.

(B) lnstitute of Geographical Sciences and Natural Resources Research, Chinese Academy of Sciences, Beijing 100010, P.R. China.

(C) College of Natural Reserve, Beijing Forestry University, Beijing 100083, P.R. China.

(D) Corresponding author. Email:
Table 1. Properties of the soils in the study area
s.d., Standard deviation; CV, coefficient of variation

Soil properties                  Mean       s.d.        CV%

SOC (%)                          35.81       3.24       9.05
TN (%)                            2.35       0.27      11.49
TP (mg/kg)                      996.35     182.87      18.35
pH                                5.22       0.17       3.26
Water content (%)                78.60       7.56       9.62
C/N ratio                        17.83       2.32      13.01
Bulk density (g/[cm.sup.3])       0.58       0.22      37.93
Clay (%)                         17.59       0.64       3.63
Silt (%)                         56.96       2.32       4.07
Sand (%)                         25.45       1.01       3.42

Table 2. Statistical analysis of densities (kg/[m.sup.2]) of soil
organic carbon density (SOCD), total nitrogen (STND), and total
phosphorus (STPD) in the study area

s.d., Standard deviation; CV, coefficient of variation

          Mean     s.d.      CV%

SOCD     62.01    21.39    34.49
STND      3.54     1.30    36.72
STPD      0.17     0.07    41.18

Table 3. Summary of geostatistical parameters for soil densities (kg/
[m.sup.2]) of organic carbon (SOCD), total nitrogen (STND), and total
phosphorus (STPD) in the drained peatland

[C.sub.0] represents the inherent nonspatially related variability in
the data (i.e. the nugget) and C represents the variability explained
by any spatial component in the data

        Model            Nugget           Sill         Range (m)
                       [C.sub.0]    [[C.sub.0] + C]

SOCD    Spherical       0.100         275.5             3.07
STND    Exponential     0.001           1.543           3.48
STPD    Spherical       0.00001         0.00396         3.15

        Model            [C.sub.0]/      [R.sup.2]
                       [[C.sub.0] + C]

SOCD    Spherical          0.0004          0.783
STND    Exponential        0.0006          0.514
STPD    Spherical          0.0025          0.518

Table 4. Correlation coefficients matrix between soil densities
of organic carbon (SOCD), total nitrogen (STND), and total
phosphorus (STPD) and selected soil properties

* P<0.05; ** P<0.01

                   SOC         TN          TP         SOCD

TN               0.317 *     1.000
TP               0.174       0.155       1.000
SOCD             0.091       0.069      -0.045       1.000
STND            -0.062       0.443 **   -0.015       0.873 **
STPD            -0.095       0.059       0.510 **    0.781 **
Soil moisture    0.191      -0.006      -0.026      -0.748 **
C/N ratio        0.370 **   -0.738 **   -0.053       0.025
BD              -0.228      -0.041      -0.099       0.945 **
pH              -0.263 *    -0.234      -0.316 **    0.157

                  STND        STPD      Soil moisture   C/N ratio

STND             1.000
STPD             0.739 **    1.000
Soil moisture   -0.715 **   -0.705 **    1.000
C/N ratio       -0.421 **   -0.110       0.133           1.000
BD               0.871 **    0.796 **   -0.795 **       -0.085
pH               0.109       0.017      -0.273 *         0.042

                Bulk density

Soil moisture
C/N ratio
BD              1.000
pH              0.230
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Author:Bai, Junhong; Ouyang, Hua; Xiao, Rong; Gao, Junqin; Gao, Haifeng; Cui, Baoshan; Huang, Laibin
Publication:Australian Journal of Soil Research
Article Type:Report
Geographic Code:9CHIN
Date:Dec 1, 2010
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