- Open Access
Compositional and chemical characteristics of dissolved organic matter in various types of cropped and natural Chinese soils
Chemical and Biological Technologies in Agriculture volume 6, Article number: 20 (2019)
Exploration of composition and chemical characteristics of soil dissolved organic matter (DOM) is significant to understand its biogeochemical role in terrestrial ecosystems. A total of 43 cropped and 16 natural soils (0–20 cm) under four soil types (cinnamon, chernozem, red and paddy soils) across China were collected to investigate the spectral characteristics of DOM using UV–Vis and 3D-EEM spectroscopy.
The chernozem soils exhibited the highest aromaticity and humification degree among the four soil types. Ranges of biological index (BIX, 0.53–1.17) and fluorescence index (FI, 1.55–2.10) were found in the investigated DOM, showing joint contribution from allochthonous and autochthonous sources. Higher BIX and FI in the DOM of the paddy and red soils indicated a greater reliance on autochthonous sources for these two soil types. The cropped soils showed no significant differences in chemical characteristics and sources from the natural soils for the cinnamon, chernozem and red soils. UVA (16.2–47.9%) and UVC fulvic-like substances (15.4–40.5%) were the prevailing DOM components, which were highest in the chernozem soils. Additionally, the cropped soils had a higher proportion of humic-like substances than the natural soils in the DOM.
Both soil type and land-use strongly affected the chemical characteristics of soil DOM, but only soil type had an impact on the DOM composition for the collected soils. These findings may contribute to the prediction of the biochemical behavior of soil DOM under different soil types and land-uses in terrestrial ecosystems.
Soil dissolved organic matter (DOM) is a mixture of various soluble organic compounds, which are mainly derived from terrestrial and autochthonous sources , including soluble substances in decaying root and leaf, root exudates, leaching or decomposition of older soil organic matter (SOM) and microbial metabolism . Despite its small content in soil, DOM is the most reactive fraction of organic matter in soils and plays a significant role in the terrestrial biogeochemical cycles [3,4,5]. Generally, soil DOM is comprised of humic-, tyrosine- and fulvic-like substances, phenolic compounds, carbohydrates, polysaccharides and N-containing molecules derived from protein and chitin [6, 7]. Due to its complex structure, DOM has been regarded as a binding hot spot for heavy metals and organic pollutants, affecting the transportation and fate of soil contaminants [8,9,10]. Moreover, many studies have reported discrepant effects of variant chemical functional groups, compositional structures and sources of DOM on the fate and transportation of heavy metals in soil [11,12,13]. Fest et al.  showed that high-molecular-size fractions promoted the combination of DOM with heavy metals. However, the enhancement of DOM with condensed humic substances has been proposed to suppress metal transportation . Therefore, it is significant to explore the composition and chemical characteristics of DOM in soil to understand its biogeochemical role.
Many researches have focused on the influence of land-use and soil type on the chemical properties, sources and composition of soil DOM [16, 17]. Chantigny et al.  reported a lower DOM concentration in the cultivation soils than in the forest and grassland soils. Some studies also observed varied chemical properties and compositions of DOM under different land-uses, especially when comparing the natural and cropped lands [19, 20]. Additionally, Gao et al.  found that the DOM in chestnut and red soils had higher aromaticity than in other soils such as chernozem and cinnamon soils. Wang et al.  also reported that DOM of a clayey soil showed a remarkably higher aromaticity and hydrophobicity than the DOM of a sandy soil. Therefore, we hypothesized that the chemical characteristics and composition of soil DOM may be affected by the land-uses and the soil types.
The objective of this study was thus to identify the chemical characteristics, sources and composition of DOM extracted from soils across China under different land-uses (natural and cropped land) and soil types (chernozem, cinnamon, red and paddy soils) using ultraviolet–visible (UV–Vis) and three-dimensional excitation–emission matrix fluorescence (3D-EEM) spectroscopy.
A total of 16 natural and 43 cropped surface soils (0–20 cm) were collected from 59 sampling sites across 19 provinces of China (Additional file 1: Table S1). Sites of four soil types (chernozem, number of samples (n) = 16; red, n = 11; cinnamon, n = 14; and paddy soil, n = 18) and two land-uses (native and cropped land) were selected as sampling locations. Maize (Zea may L.), zucchini (Cucurbita pepo L.), oilseed rape (Brassica campestris L.) and rice (Oryza sativa L.) were grown in the croplands, while the natural lands were mainly forest and grasslands. Detailed climatic, vegetation and sampling information is given in Additional file 1: Table S1. Three soil samples were collected from each sampling site and thoroughly mixed into one sample. The soils were then transported to the laboratory immediately. The samples were freeze-dried after removing roots and gravel and then ground to pass through 2- and 0.15-mm nylon sieves.
Soil characterization and DOM extraction
Soil pH was measured with a S20K pH meter (Mettler Toledo, Switzerland) in a soil/water ratio of 1:2.5. SOM content was determined by the wet H2SO4–K2Cr2O7 oxidation method . Cation-exchange capacity (CEC) was detected using the ammonium acetate (NH4COOH) method . An elemental analyzer (Elementar, Germany) was used to determine the total nitrogen (TN) and carbon (TC) in the soils. The contents of dissolved organic carbon (DOC) and nitrogen (DON) were measured by the method described by Jones and Willett .
The extraction of soil DOM was performed referring to a simply modified method described by Gao et al. . In brief, 4 g of freeze-dried soil was mixed with deionized water with a soil/water ratio of 1:10 in a 50-ml centrifuge tube. The mixture was shaken under N2 environment at 25 °C for 18 h and then centrifuged at 8000g and 25 °C for 20 min. After a filtration through a 0.45-μm glass fiber filter, the solution of DOM was obtained and stored at − 20 °C until analysis.
UV–Vis and 3D-EEM spectroscopy
In order to avoid inner-filter effects on fluorescence and UV–Vis analysis, the concentrations of total organic carbon (TOC) in the DOM solutions were uniformly diluted to 10 mg/l prior to determination . UV–Vis spectra of the DOM sample in a 1-cm quartz cuvette were recorded on a UV-2802 spectrometer (UNICO, UK) with a scanning wavelength of 254 nm. Deionized water was used as a measurement blank for the UV–Vis spectral analysis. SUVA254 was calculated by dividing the UV absorbance at wavelength of 254 nm by the DOC concentration to indicate the relative contents of aromatic compounds .
A F7000 fluorescence spectrometer (Hitachi, Japan) was employed to create EEMs for the DOM samples based on measurement of fluorescence intensity at emission wavelengths ranging from 200 to 480 nm and excitation wavelengths ranging from 200 to 450 nm. The fluorescence spectra were scanned with a slit width of 5 nm and a scanning speed of 2400 nm/min. Parallel factor analysis (PARAFAC) was applied using the DOMFluor toolbox on MATLAB R2016a (Mathworks, USA) to identify outlier and eliminate the Raman scattering effect on the EEM spectra . Residual and split-half analyses were further conducted to validate fluorescence components of DOM . Spectral indices were calculated from the fluorescence EEMs, following the previously reported definitions for fluorescence index (FI) , biological index (BIX)  and humification index (HIX) . In brief, FI and BIX were calculated by the ratios of fluorescence intensity at emission wavelengths of 470 nm and 520 nm (excitation wavelength of 370 nm) and at emission wavelengths of 380 nm 430 nm (excitation wavelength of 310 nm), respectively . HIX was defined as the inner-filter corrected fluorescence intensity in the 435–480-nm region divided by the sum of fluorescence intensity in the regions of 300–345 nm and 435–480 nm . HIX has been widely employed to indicate the humification index in DOM [26, 32]. FI is typically used to distinguish the autochthonous (FI > 1.9) and from allochthonous (FI < 1.4) sources of DOM , while BIX reflects on recently produced autochthonous (biological) DOM .
One-way analysis of variance (ANOVA) was performed using SPSS v24.0 (IBM, USA) to test the significant differences in soil physicochemical properties and spectral characteristics of DOM under different land-uses and soil types. Correlations of soil properties with spectral indices and fluorescence components of DOM were conducted using SPSS v24.0 (IBM, USA). Two-way ANOVA was employed using SPSS v24.0 (IBM, USA) to investigate the effects of soil types and land-uses on the spectral indices and fluorescence components in the DOM. A redundancy analysis (RDA) was performed with XLSTAT v2012 software (Addinsoft, USA) to detect the multivariate relationships among soil properties, spectral indices and DOM components.
Soil pH ranged from 4.47 to 9.18 with an average of 6.52 (Table 1). The cinnamon (7.96 ± 0.89) and chernozem soils (7.82 ± 0.80) had higher pH than the red (6.44 ± 1.49) and paddy soils (6.71 ± 1.17). No significant difference in soil pH in between natural and cropped soils was found. The SOM content was 4.07% ± 1.51% with the highest SOM detected in the chernozem soils (6.61% ± 3.38%). The SOM content in the natural soils was higher than in the cropped soils (Table 1). The CEC in the soils was 28.60 cmol/kg on average with a range from 6.23 to 49.25 cmol/kg, while the chernozem soils had the highest CEC (32.12 ± 8.28 cmol/kg). A range of soil TN from 0.04 to 0.58% was detected with higher TN in the cropped soils than in the natural soils. TC content for all the soils ranged from 0.33% to 7.95% with an average of 1.86%. No significant differences in TN, TC and TC/TN ratio were found in between the four soil types (Table 1). The DOC and DON were 0–0.36 mg/g and 0–0.05 mg/g in all the soils with a DOC/DON ratio ranging from 1.4 to 16.3. The paddy soils had the lowest DOC (0.08 ± 0.08 mg/g) and DON (0.01 ± 0.01 mg/g).
UV–Vis and 3D-EEM spectroscopy
As calculated from UV–Vis spectra for the DOM samples, SUVA254 values ranged from 0 to 3.1 with an average of 1.49 (Table 2). The highest and lowest SUVA254 were found in the DOM of the chernozem (2.03 ± 0.48) and paddy soils (1.10 ± 0.54), respectively. HIX index was found to be 0.77 ± 0.10 in the DOM samples. The DOM of the chernozem (0.92 ± 0.02) and cinnamon soils (0.86 ± 0.03) possessed the higher HIX index than that of the paddy (0.79 ± 0.05) and red soils (0.75 ± 0.14). The spectral indices of BIX and FI for all the soil DOM were 0.61–1.17 and 1.55–2.10, respectively. The BIX and FI of the DOM in the chernozem and cinnamon soils were significantly (P < 0.05) lower than in the red and paddy soils. Very few DOM samples had FI exceeding 1.9 and BIX higher than 1.0. No significant differences in spectral indices were found in between the natural and the cropped soils (Table 2).
As shown in Fig. 1, five fluorescence components (C1–C5) were identified by the PARAFAC of all the DOM samples and assigned to be: UVA fulvic-like substances (C1, Ex/Em = 265/460 nm) [27, 28], UVC fulvic-like substances (C2, Ex/Em = 230/400 nm) , humic-like substances (C3, Ex/Em = 320 (250)/400 nm) [35, 36], tryptophan-like substances (C4, Ex/Em = 230 (275)/330 nm)  and peptide-like compounds (C5, Ex/Em = 220/330 nm) [1, 4, 38].
C1 (16.2%–47.9%) and C2 (15.4%–40.5%) were the prevailing fluorescence components in the DOM (Fig. 2), while C5 was the lowest component accounting for 0–24.7%. The chernozem soils had the highest proportion of C1 (36.3%–47.9%) and the lowest proportion of C4 (3.7%–14.3%), while the red soils possessed the highest and lowest proportions of C3 (13.6%–23.7%) and C5 (0–7.5%), respectively. Higher proportion of C4 and lower proportion of C2 were observed in the red and paddy soils than in the chernozem and cinnamon soils (Fig. 2). The cropped chernozem and red soils had higher proportion of C1 and C3 but lower proportion of C4 than the natural soils. As for the cinnamon soils, the cropped soils occupied higher shares of C2 (21.6%–40.5%) and C3 (10.8%–13.6%) in the total DOM than the natural soils (28.4%–30.6% for C2 and 8.1%–10.4% for C3).
Relationship of DOM composition and spectral indices with soil properties
DOC and SOM were significantly positively (P < 0.01) correlated with SUVA254 in the soil DOM but negatively correlated with the BIX and FI (Fig. 3). No significant correlations of the TC, TN and CEC with spectral indices were found. Among the spectral indices for the DOM samples, SUVA254 and HIX possessed significantly negative correlations with BIX and FI, while SUVA254 had a positive relationship with HIX. FI and BIX showed negative correlations (P < 0.01) with the proportions of C1 and C2 and positive correlations (P < 0.01) with the proportions of C3 and C4 in the DOM (Fig. 3). Conversely, soil pH and the HIX of DOM were positively correlated (P < 0.01) with the proportions of C1 and C2 and negatively correlated (P < 0.01) with the proportion of C4.
The RDA plot reported in Fig. 4 reveals multiple relationships among soil properties, spectral indices and fluorescence components of the soil DOM. The axes of RD1 and RD2 explained 60.27% and 32.24% of the total variation, respectively. Along the RD1, a net differentiation of the paddy soils from the cinnamon and chernozem soils was detected and ascribed to the different DOM compositions. Additionally, the natural soils for the chernozem, red and cinnamon soils were neatly separated from the cropped soils of these three soil types along the RD1. Along the RD2, a distinct separation of the red soils from the other three types of soils was observed. Two-way ANOVA showed a significant effect (P < 0.001) of soil types on the spectral indices and the fluorescent components of the DOM (Table 3). Land-uses (cropped and natural land) and its intercept with soil types did not significantly affect (P > 0.05) the spectral indices, but had an impact on the fluorescence components of C1, C4 and C5.
Effect of soil types on the spectral characteristics of soil DOM
Most of the collected chernozem and cinnamon soils were alkalic, whereas a majority of the red and paddy soil samples showed weak acidity (Table 1). These results are in line with previous studies [39, 40]. It has been proposed that the chernozem soils had higher SOM abundance than the cinnamon, red and paddy soils on a countrywide scale , which was also observed in the present study. Lower input of organic matter and stronger decomposition of SOM may contribute to the lower SOM in the cropped soils than in the natural soils (Table 1) . Higher CEC and TN detected in the cropped soils than in the natural soils may be due to fertilization during the cropping management [43, 44]. The range of the DOC content in the investigated soils was in line with previous studies [1, 45].
Among the four soil types, the DOM extracted from the chernozem soils possessed the highest SUVA254 and HIX, showing the highest degrees of aromaticity and humification (Table 2). By contrast, the lowest SUVA254 and HIX were detected in the DOM from the paddy and red soils and indicated the lowest aromaticity and humification degrees. A previous study has also reported a higher aromaticity in several chernozem soils than in the red soils . This may be attributed to the higher SOM found in the chernozem soils than in the paddy and red soils (Table 1), and the decomposition and humification of SOM may induce an accumulation of aromatic compounds in the chernozem soils . Additionally, positive correlations of HIX and SUVA254 with DOC (Fig. 3) may hint that DOC served as a significant C source for the growth of soil microbiome and favored the decomposition and humification of SOM in soil [6, 47]. FI and BIX of the soil DOM were mainly distributed in the ranges of 1.4 < FI < 1.9 and 0.6 < BIX < 1.0 (Table 2) and suggested a joint contribution of DOM from microbial and allochthonous sources [7, 48]. The DOM of the paddy and red soils had lower BIX and FI than that of the chernozem and cinnamon soils, showing greater autochthonous sources which may be due to stronger microbial activity . BIX had a positive relationship with FI (P < 0.01, Fig. 3), which is in line with a previous study of Jiang et al. . In general, SUVA254, BIX, HIX and FI of the DOM varied with different soil types (Table 2). In addition, the two-way ANOVA also suggested a strong effect of soil types on the spectral indices of the soil DOM (Table 3).
Despite a wide range of soil physicochemical properties (Table 1), fulvic-like substances were the prevailing fluorescence components in the soil DOM, which is in line with a previous study of Ren et al. . As shown in Fig. 2, various soil types had different distributions of DOM fluorescence components in the collected soils. The chernozem and cinnamon soils possessed higher proportion of UVA (C1) and UVC (C2) fulvic-like substances, which have been proposed to be mainly derived from allochthonous sources . Meanwhile, tryptophan-like substances (C4) in the DOM were thought to be mainly derived from autochthonous sources  and were positively correlated with BIX and FI in the present study (Fig. 3). The proportion of tryptophan-like substances in the DOM were lower in the chernozem and cinnamon soils than in the paddy and red soils (Fig. 2b), therefore indicating a relatively low DOM contribution from autochthonous sources. This is in accord with the lower BIX and FI (Table 2) detected in the DOM of the chernozem and cinnamon soils. The red soils exhibited the highest relative abundance of humic-like substances (C4, Fig. 2b), which may be explained by the fact that the red soils were often Fe-rich and the complexation of Fe with DOC may suppress the decomposition of humic substances . The paddy soils had the highest proportion of peptide-like substances (C5), which are usually considered as autochthonous and represent the magnitude of the biological and microbial activities . It is worth noting that the two-way ANOVA showed a great effect of the soil types on the DOM composition (Table 3). The RDA plot also revealed that the fluorescence components of the DOM were strongly affected by the sources and chemical characteristics of the DOM and the soil properties for different soil types (Fig. 4).
Effect of land-use on the spectral characteristics of soil DOM
For the DOM spectral indices of SUVA254, HIX, FI and BIX, no significant (P > 0.05) differences were found in between the natural and the cropped soils (Table 2). This was confirmed by the two-way ANOVA, which showed that no significant (P > 0.05) effect of land-use on the spectral indices of the DOM was detected (Table 3). However, it has been reported by previous studies  that the cropped soils exhibited distinct differences in humification, aromaticity and sources of the DOM from the natural soils. The great spatial variability of chemical characteristics and sources of the DOM in a large scale may contribute to the discrepant results from the present study.
In comparison with the cropped soils, the natural soils possessed higher proportion of UVA and UVC fulvic-like and humic-like substances in the DOM for the chernozem, cinnamon and red soils (Fig. 2c, d). This is in line with Zhang et al.  showing that more fulvic- and humic-like compounds are detected when the land-use is changed from natural land to farmland. In contrast, the DOM of the natural chernozem soils had higher proportions of tryptophan- and peptide-like substances than the cropped chernozem soils. A higher proportion of peptide-like substances in the cropped cinnamon soils and a higher proportion of tryptophan-like substances in the cropped red soils were also found in comparison with the corresponding natural soils. This may be due to a lower input and a faster decomposition of the SOM in the cropped soils [53, 54]. The removal of above-ground biomass of crops by harvesting reduced the input of plant residues, and therefore, DOM in the cropped soil relied more on allochthonous sources . Organic amendments, such as straw application, use of manure and organic conditioners, may alter the composition and characteristics of DOM [20, 33]. Conversely, more easily decomposed litter and roots entered the natural soils and improved the microbial activity to accelerate SOM transformation which could accumulate more microbial metabolites, such as peptide- and tryptophan-like substances . For the cinnamon, chernozem and red soils, the RDA also showed a neat separation of the cropped soils from the natural soils, indicating an important impact of land-uses on the DOM compositions. The two-way ANOVA revealed that most of the soil DOM components were affected by land-use and land-use × soil type.
Here, we conducted spectral analyses of the soil DOM extracted from 59 natural and cropped soils across China under four different soil types to investigate the chemical characteristics, sources and composition of DOM. The results showed that DOM of the chernozem and cinnamon soils exhibited the highest aromaticity and humification degree. Allochthonous and autochthonous sources jointly contributed to the DOM from the investigated soils; however, the DOM in the paddy and red soils was derived more from autochthonous sources. The cropped soils showed no significant differences in chemical characteristics and sources from the natural soils for the cinnamon, chernozem and red soils. UVA and UVC fulvic-like substances were the prevailing fluorescence components in the DOM samples. The DOM of the chernozem soils had the highest proportions of UVA and UVC fulvic-like substances, while the DOM of red soils possessed the highest humic- and tryptophan-like substances. In contrast to the natural soils, the cropped soils had higher proportion of humic-like substances but a lower proportion of tryptophan-like substances in their DOM. RDA and two-way ANOVA showed that soil types and land-use strongly affected the chemical characteristics of the soil DOM, but soil types had also an impact on the DOM composition. The findings of this study prove the heterogenous nature of the corresponding DOM under various soil types and land-uses. Only by taking in account DOM variability may we deepen our knowledge in order to predict the biochemical behavior of soil DOM in the terrestrial ecosystems to prevent the losses of soil fertility and to avoid soil pollution from spreading.
Availability of data and materials
All data are presented in the manuscript.
dissolved organic matter
three-dimensional excitation–emission matrix fluorescence
parallel factor analysis
dissolved organic carbon
dissolved organic nitrogen
total organic carbon
analysis of variance
Gao J, Liang C, Shen G, Lv J, Wu H. Spectral characteristics of dissolved organic matter in various agricultural soils throughout China. Chemosphere. 2017;176:108–16.
McDowell WH. Dissolved organic matter in soils: future directions and unanswered questions. Geoderma. 2003;113:179–86.
Scott EE, Rothstein DE. The dynamic exchange of dissolved organic matter percolating through six diverse soils. Soil Biol Biochem. 2014;69:83–92.
Yamashita Y, McCallister SL, Koch BP, Gonsior M, Jaffé R. Dynamics of dissolved organic matter in fjord ecosystems: contributions of terrestrial dissolved organic matter in the deep layer, Estuari. Coast Shelf Sci. 2015;159:37–49.
Chen M, Kim S, Park J-E, Kim HS, Hur J. Effects of dissolved organic matter (DOM) sources and nature of solid extraction sorbent on recoverable DOM composition: implication into potential lability of different compound groups. Anal Bioanal Chem. 2016;408:4809–19.
Kaiser K, Kalbitz K. Cycling downwards—dissolved organic matter in soils. Soil Biol Biochem. 2012;52:29–32.
Jiang T, Kaal J, Liang J, Zhang Y, Wei S, Wang D, Green NW. Composition of dissolved organic matter (DOM) from periodically submerged soils in the Three Gorges Reservoir areas as determined by elemental and optical analysis, infrared spectroscopy, pyrolysis-GC–MS and thermally assisted hydrolysis and methylation. Sci Total Environ. 2017;603–604:461–71.
Aiken GR, Hsu-Kim H, Ryan JN. Influence of dissolved organic matter on the environmental fate of metals, nanoparticles, and colloids. Environ Sci Technol. 2011;45:3196–201.
Hu S, Lu C, Zhang C, Zhang Y, Yao H, Wu Y. Effects of fresh and degraded dissolved organic matter derived from maize straw on copper sorption onto farmland loess. J Soil Sediment. 2016;16:327–38.
Yuan DH, An YC, He XS, Yan CL, Jia YP, Wang HT, He LS. Fluorescent characteristic and compositional change of dissolved organic matter and its effect on heavy metal distribution in composting leachates. Environ Sci Pollut Res. 2018;25:18866–78.
Jiang T, Chen XS, Wang DY, Liang J, Bai WY, Zhang C, Wang QL, Wei SQ. Dynamics of dissolved organic matter (DOM) in a typical inland lake of the Three Gorges Reservoir area: fluorescent properties and their implications for dissolved mercury species. J Environ Manage. 2018;206:418–29.
Wu J, Zhang H, Shao LM, He PJ. Fluorescent characteristics and metal binding properties of individual molecular weight fractions in municipal solid waste leachate. Environ Pollut. 2012;162:63–71.
Amery F, Degryse F, Cheyns K, De Troyer I, Mertens J, Merckx R, Smolders E. The UV-absorbance of dissolved organic matter predicts the fivefold variation in its affinity for mobilizing Cu in an agricultural soil horizon. Eur J Soil Sci. 2008;59:1087–95.
Fest EPMJ, Temminghoff EJM, Comans RNJ, Riemsdijk WH. Partitioning of organic matter and heavy metals in a sandy soil: effects of extracting solution, solid to liquid ratio and pH. Geoderma. 2008;146:66–74.
Benedetti MF, Van Riemsdijk WH, Koopal LK. Humic substances considered as a heterogeneous donnan gel phase. Environ Sci Technol. 1996;30:1805–13.
Bolan NS, Adriano DC, Kunhikrishnan A, James T, McDowell R, Senesi N. Dissolved organic matter: biogeochemistry, dynamics, and environmental significance in soils. Adv Agron. 2011;110:1–75.
Yang L, Hong H, Guo W, Huang J, Li Q, Yu X. Effects of changing land use on dissolved organic matter in a subtropical river watershed, southeast China. Reg Environ Change. 2012;12:145–51.
Chantigny MH. Dissolved and water-extractable organic matter in soils: a review on the influence of land use and management practices. Geoderma. 2003;113:357–80.
Seifert AG, Roth VN, Dittmar T, Gleixner G, Breuer L, Houska T, Marxsen J. Comparing molecular composition of dissolved organic matter in soil and stream water: influence of land use and chemical characteristics. Sci Total Environ. 2016;571:142–52.
Celik I. Land-use effects on organic matter and physical properties of soil in a southern Mediterranean highland of Turkey. Soil Till Res. 2005;83:270–7.
Wang B, Zeng D, Chen Y, Belzile N, Baid Y, Zhua J, Shu J, Chen S. Adsorption behaviors of phenanthrene and bisphenol A in purple paddy soils amended with straw-derived DOM in the West Sichuan Plain of China. Ecotoxicol Environ Safe. 2019;169:737–46.
Nelson D, Sommer L. Total carbon, organic carbon, and organic matter. In: Page AL, Miller RH, Keeney DR, editors. Methods of soil analysis. Madison: American Society of Agronomy and Soil Science Society of American; 1982. p. 539–79.
Chapman HD. Cation–exchange capacity. In: Chernozem CA, editor. Methods of soil analysis. Part 2: Chemical and microbiological properties. Madison: American Society of Agronomy; 1965. p. 891–900.
Jones DL, Willett VB. Experimental evaluation of methods to quantify dissolved organic nitrogen (DON) and dissolved organic carbon (DOC) in soil. Soil Biol Biochem. 2006;38:991–9.
Rodríguez FJ, Schlenger P, García-Valverde M. Monitoring changes in the structure and properties of humic substances following ozonation using UV–Vis, FTIR and 1H NMR techniques. Sci Total Environ. 2016;541:623–37.
Weishaar JL, Aiken GR, Bergamaschi BA, Fram MS, Fujii R, Mopper K. Evaluation of specific ultraviolet absorbance as an indicator of the chemical composition and reactivity of dissolved organic carbon. Environ Sci Technol. 2003;37:4702–8.
Chen W, Westerhoff P, Leenheer JA, Booksh K. Fluorescence excitation–emission matrix regional integration to quantify spectra for dissolved organic matter. Environ Sci Technol. 2003;37:5701–10.
Stedmon CA, Bro R. Characterizing dissolved organic matter fluorescence with parallel factor analysis: a tutorial. Limnol Oceanogr Methods. 2008;6:572–9.
Mcknight DM, Boyer EW, Westerhoff PK, Doran PT, Kulbe T, Andersen DT. Spectrophotometric characterization of dissolved organic matter for indication of precursor organic material and aromaticity. Limnol Oceanogr. 2001;46:38–48.
Huguet A, Vacher L, Relexans S, Saubusse S, Froidefond JM, Parlanti E. Properties of fluorescent dissolved organic matter in the Gironde estuary. Org Geochem. 2009;40:706–19.
Ohno T. Fluorescence inner-filtering correction for determining the humification index of dissolved organic matter. Environ Sci Technol. 2002;3:742–6.
Hur J, Lee BM, Shin HS. Microbial degradation of dissolved organic matter (DOM) and its influence on phenanthrene–DOM interactions. Chemosphere. 2011;85:1360–7.
Wilson HF, Xenopoulos MA. Effects of agricultural land use on the composition of fluvial dissolved organic matter. Nat Geosci. 2009;2:37–41.
Cory RM, Mcknight DM. Fluorescence spectroscopy reveals ubiquitous presence of oxidized and reduced quinones in dissolved organic matter. Environ Sci Technol. 2005;39:8142–9.
Stedmon CA, Markager S. Resolving the variability in dissolved organic matter fluorescence in a temperate estuary and its catchment using PARAFAC analysis. Limnol Oceanogr. 2005;50:686–97.
Kowalczuk P, Tilstone GH, Zabłocka M, Röttgers R, Thomas R. Composition of dissolved organic matter along an Atlantic meridional transect from fluorescence spectroscopy and parallel factor analysis. Mar Chem. 2013;157:170–84.
Yuan DH, Guo N, Guo XJ, Zhu NM, Chen L, He LS. The spectral characteristics of dissolved organic matter from sediments in lake Baiyangdian, North China. J Great Lakes Res. 2014;40:684–91.
Li WT, Chen SY, Xu ZX, Li Y, Shuang CD, Li AM. Characterization of dissolved organic matter in municipal wastewater using fluorescence PARAFAC analysis and chromatography multi-excitation/emission scan: a comparative study. Environ Sci Technol. 2014;48:2603–9.
Liu Y, Xu Z, Wu X, Gui W, Zhu G. Adsorption and desorption behavior of herbicide diuron on various Chinese cultivated soils. J Hazard Mater. 2010;178:462–8.
Zhang Y, Yang X, Zhang S, Tian Y, Guo W, Wang J. The influence of humic acids on the accumulation of lead (Pb) and cadmium (Cd) in tobacco leaves grown in different soils. J Soil Sci Plant Nut. 2013;13:43–53.
Gu Z, Xie Y, Gao Y, Ren X, Cheng C, Wang S. Quantitative assessment of soil productivity and predicted impacts of water erosion in the chernozem soil region of northeastern China. Sci Total Environ. 2018;637–638:706–16.
Qiu L, Wei X, Ma T, Wei Y, Horton R, Zhang X, Cheng J. Effects of land-use change on soil organic carbon and nitrogen in density fractions and soil δ13 C and δ15 N in semiarid grasslands. Plant Soil. 2015;390:419–30.
Guo Z, Zhang J, Fan J, Yang X, Yi Y, Han X, Wang D, Zhu P, Peng X. Does animal manure application improve soil aggregation? Insights from nine long-term fertilization experiments. Sci Total Environ. 2019;660:1029–37.
Gai X, Liu H, Liu J, Zhai L, Wang H, Yang B, Ren T, Wu S, Lei Q. Contrasting impacts of long-term application of manure and crop straw on residual nitrate-N along the soil profile in the North China Plain. Sci Total Environ. 2019;650:2251–9.
Li G, Khan S, Ibrahim M, Sun TR, Tang JF, Cotner JB, Xu YY. Biochars induced modification of dissolved organic matter (DOM) in soil and its impact on mobility and bioaccumulation of arsenic and cadmium. J Hazard Mater. 2018;348:100–8.
Kalbitza K, Schwesig D, Schmerwitza J, Kaiserb K, Haumaierc L, Glaserc B, Ellerbrockd R, Leinwebere P. Changes in properties of soil-derived dissolved organic matter induced by biodegradation. Soil Biol Biochem. 2003;35:1129–42.
Wang J, Wu Y, Zhou J, Bing H, Sun H. Carbon demand drives microbial mineralization of organic phosphorus during the early stage of soil development. Biol Fert Soils. 2016;526:825–39.
Birdwell JE, Enge AS. Characterization of dissolved organic matter in cave and spring waters using UV–Vis absorbance and fluorescence spectroscopy. Org Geochem. 2010;41:270–80.
Huang W, Mcdowell WH, Zou X, Ruan H, Wang J, Ma Z. Qualitative differences in headwater stream dissolved organic matter and riparian water-extractable soil organic matter under four different vegetation types along an altitudinal gradient in the Wuyi Mountains of China. Appl Geochem. 2015;52:67–75.
Ren ZL, Tella M, Bravin MN, Comans RNJ, Dai J, Garnier JM, Sivry Y, Doelsch E, Straathof A, Benedetti MF. Effect of dissolved organic matter composition on metal speciation in soil solutions. Chem Geol. 2015;398:61–9.
Drosos M, Piccolo A. The molecular dynamics of soil humus as a function of tillage. Land Degrad Dev. 2018;29:1792–805.
Zhang J, Song C, Yang W. Land use effects on the distribution of labile organic carbon fractions through soil profiles. Soil Sci Soc Am J. 2006;70:660–7.
Lepane V, Depret L, Väli AL, Suursööt K. Impact of seasonal climate change on optical and molecular properties of river water dissolved organic matter by HPLC–SEC and UV–vis spectroscopy. Chem Biol Technol Agric. 2015;2:14.
Hanke A, Cerli C, Muhr J, Borken W, Kalbitz K. Redox control on carbon mineralization and dissolved organic matter along a chronosequence of paddy soils. Eur J Soil Sci. 2013;64:476–87.
The authors thank Mr. Chao Yang, Dr. Xiangru Zhang, Mr. Guang Yang, Mr. Zhurui Tang and the staffs at Qiyang red soil station for their assistance in soil sampling.
No funding is available.
Ethics approval and consent to participate
The manuscript is an original work that has not been published in other journals. The authors declare no experiments involving humans and animals.
Consent for publication
All authors agreed to the publication.
The authors declare that they have no competing interests.
Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
About this article
Cite this article
Li, S., Li, M., Wang, G. et al. Compositional and chemical characteristics of dissolved organic matter in various types of cropped and natural Chinese soils. Chem. Biol. Technol. Agric. 6, 20 (2019). https://doi.org/10.1186/s40538-019-0158-z
- Water-soluble organic matter
- Soil type
- Three-dimensional excitation–emission matrix fluorescence (3D-EEM) spectroscopy
- Parallel factor analysis (PARAFAC)
- Spectral indices