| HOME | HELP | FEEDBACK | SUBSCRIPTIONS | ARCHIVE | SEARCH | TABLE OF CONTENTS |
|
|
|
|||||||
|
|||||||||
a Dep. of Soil, Water, and Environmental Science, Univ. of Arizona, 1177 E. Fourth St., P.O. Box 210038, Shantz Bldg. #38, Tucson, AZ 85721-0038
b Lawrence Berkeley National Lab., Center for Isotope Geochemistry, One Cyclotron Road MS 90-1116, Berkeley, CA 94720
c Land, Air and Water Resources Dep., Univ. of California, One Shields Avenue, Davis, CA 95616
* Corresponding author (crasmuss{at}ag.arizona.edu)
 |
ABSTRACT |
|---|
 TOP ABSTRACT INTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
Abbreviations: AMS, accelerator mass spectrometry • AN, andesite-granite • DI, deionized • GR, granite • HIV, hydroxy-interlayered vermiculite • MRT, mean residence time • PSA, particle-size analysis • SPT, sodium polytungstate • SRO, short-range order • subscript d, citrate dithionite extract • subscript o, ammonium oxalate extract • subscript p, sodium pyrophosphate extract • XRD, x-ray diffraction
|
INTRODUCTION |
|---|
|
TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
Key variables controlling C stabilization include climate, soil texture, mineral assemblage, organomineral associations and aggregate stability (Oades, 1988; Golchin et al., 1994; Feller and Beare, 1997; Six et al., 2000). Soil mineral assemblage and soil chemical properties, such as mineral charge, reactive surface area, and polyvalent cations, influence both C adsorption capacity as well as aggregate protection of C. It has been suggested that in many soils, the type of soil mineral assemblage is more important to soil C storage than the total amount of clay (Veldkamp, 1994; Torn et al., 1997; Percival et al., 2000). Soils derived from andesitic parent materials, in particular, show exceptionally high soil C stocks that have been attributed to soil mineral properties. Short range order minerals common to soils derived from andesite, such as allophane, imogolite, and ferrihydrite, have a propensity to complex humic substances through ligand exchange between mineral hydroxyl groups and humic substance functional groups (Yuan et al., 2000). Dissolved organic carbon (DOC) adsorption has been shown to increase with increasing SRO content (Lilienfein et al., 2004), and SRO minerals may act to stabilize microbial biomass and metabolites (Zunino et al., 1982; Saggar et al., 1996). Parfitt et al. (2002) and Torn et al. (1997) showed increased stability of soil C in Andisols compared with Inceptisols and other soil orders, and suggested that SRO minerals are responsible for this greater stability and MRT.
Organic substances may associate with soil minerals by direct adsorption to mineral surfaces through cation or anion exchange, H-bonding, van der Waal's forces, ligand exchange reactions, or bridging by polyvalent cations (e.g., organometal–clay complexes) (Theng, 1979; Stevenson, 1994). Iron (III) and Al3+ form strong coordination complexes with humic substances and are likely the most important cations for bridging the negative charge of mineral and organic surfaces in well drained, neutral to acidic soils. Short range order Al and Fe sesquioxides and organometal complexes (in particular Al-humus complexes) appear to be strongly correlated with C stabilization in many soil systems (Veldkamp, 1994; Shang and Tiessen, 1998; Percival et al., 2000; Masiello et al., 2004). Greater organometal complexation may promote stability of mineral-associated C by providing numerous bridging points between the organic molecule and mineral surface or through metal inhibition of microbial decomposition. It has also been suggested that soil mineral assemblage acts as a control of aggregate formation and stability through both mineral-mineral interactions and organomineral complex interactions (Oades and Waters, 1991; Six et al., 2000).
The objective of this study was to characterize the influence of soil mineral assemblage on the partitioning of C into density and aggregate fractions and the MRT of C in these fractions. Specifically, the aim of the research was to quantify the relationship between Fe- and Al-oxyhydroxide, Al-humus complex and soil C content, and soil C MRT in soils containing similar crystalline mineral assemblages. We studied mature second growth conifer ecosystems in the Sierra Nevada of California because they represent a major part of the regional C budget of the western USA. Further, the majority of these forest systems are actively managed by both private and governmental agencies allowing for the potential to manage for terrestrial C storage.
|
MATERIALS AND METHODS |
|---|
|
TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
We selected two forest stands of similar stand age (80–90 yr) and similar management histories (Robert Heald, Blodgett Station Manager, personal communication, 2001), dominated by Pinus ponderosa. The stands are separated by <1.6 km, occur at elevations between 1300 and 1350 m on similar slopes (<10%), aspects (west to southwest), and micro-climate regimes. Soils of the two stands have a xeric soil moisture regime and mesic soil temperature regime, but are derived from different soil parent materials, mixed andesite-granite (AN) and granite (GR). Granite soils are mapped (USDA, 1985) as part of the Holland-Bighill complex map unit (Holland: fine-loamy, mixed, superactive, mesic Ultic Haploxeralfs and Bighill: coarse-loamy, mixed, superactive mesic Humic Dystroxerepts) derived from Mesozoic granodiorite (Jennings, 1977). Andesite-granite soils are mapped (USDA, 1985) as part of the Cohasset map unit (fine-loamy, mixed, superactive, mesic Ultic Haploxeralf) formed from weathered andesitic lahar. However, while the AN site appears to have been overlain by andesitic parent materials in the past, much of this material has since been eroded, so that present soils contain a mix of andesite and granite parent materials.
We sampled three pedons per stand, each pedon separated by more than 15 m. Pedons were sampled to a depth of approximately 80 cm, the base of the BC horizon. Sample locations in both stands shared similar landform attributes (slope and aspect) and were representative of the soils and vegetation of each stand. The morphology of each pedon was described in the field, and soil samples were collected by morphologic horizon for each pedon. Collected soils were allowed to air dry, then sieved at 2 mm. All analyses were performed on the <2-mm fraction of each horizon, unless otherwise stated.
Bulk Soil Characterization
Bulk density was measured in the field using a hammer corer device (Blake and Hartge, 1986) for one pedon in each stand. Three cores were taken from each horizon. Sample weight and volume were corrected for coarse fragment content (USDA, 1996). Soil pH was measured 1:1 in H2O and 1:2 in 0.2 M CaCl2 (USDA, 1996).
Particle-size analysis (PSA) was determined by the pipette method and wet sieving (National Soil Survey Manual, 1996). Samples were pretreated with sodium hypochlorite to remove organic matter (Anderson, 1963) and dispersed in sodium-hexametaphosphate. Dispersed samples were wet sieved at 53 µm, and clay and silt collected in 1-L cylinders for pipette analysis. Sands (>53 µm) were collected, dried at 105°C and weighed. All mass percentage calculations are reported on an oven dry basis.
Mineralogy
Mineralogical analysis by x-ray diffraction (XRD) was conducted on the clay (<2 µm), silt (2–53 µm), and very fine sand (53–100 µm) fractions for each horizon of the central pedon from each stand. Clays and silts were fractionated by repeated mixing and centrifugation with dilute Na2CO3. X-ray analyses were made with a Diano XRD 8000 diffractometer (Diano, Woburn, MA) producing Cu-K
radiation. Clays and silts were oriented and mounted on glass slides with the following standard treatments: Mg saturation, Mg saturation/glycerol solvation, K saturation, and heat treatment of K-saturated samples at 350 and 550°C (Whittig and Allardice, 1986). Sodium-saturated very fine sands were analyzed using random powder mounts.
Selective dissolution was performed on bulk soil using standard methods of acid ammonium oxalate, sodium pyrophosphate, and citrate dithionite extraction (USDA, 1996). Extractions were performed on each horizon of every pedon and were not sequential. Soil samples were shaken for 4 h in the dark with a soil/oxalate ratio of 1:100 with 0.2 M acid ammonium-oxalate adjusted to pH 3.0. Following extraction, samples were centrifuged at 1180 x g for 10 min with addition of 2 mL of 0.1% flocculating agent (Superfloc, American Cyanamid Co., Wayne, NJ) (Dahlgren, 1994). Oxalate predominantly extracts Al, Fe, and Si (Alo, Feo, Sio) from organic complexes and SRO Fe-oxyhydroxides (e.g., ferrihydrite) and aluminosilicates (e.g., allophane and imogolite).
Soil samples were shaken for 15 h with 0.1 M sodium pyrophosphate pH 10 at a soil to liquid ratio of 1:100. After shaking, samples were centrifuged at 51 248 x g for 30 min after adding 2 mL of 0.1% Superfloc to isolate the supernatant and avoid contamination of the supernatant with peptised material (Dahlgren, 1994). Pyrophosphate predominantly extracts Al and C (Alp, Cp) bound in organometal complexes. We used Alp as an index of Al-humus complexes.
Dithionite extraction consisted of shaking 4 g of soil for 15 h with 2 g of sodium dithionite and 100 mL of 0.3 M sodium citrate. The suspension was centrifuged at 1180 x g for 10 min following addition of 2 mL of 0.1% Superfloc (Dahlgren, 1994). Citrate dithionite is reported to extract Fe and Al (Fed, Ald) from organic complexes, some SRO aluminosilicates, and secondary forms of Fe-oxyhydroxides (Parfitt and Childs, 1988; Dahlgren, 1994).
Silicon, Al, and Fe from each extraction procedure were measured by atomic absorption spectrometry (AAS) (AA8000, PerkinElmer, Wellesley, MA). Supernatant from each extraction were filtered through Whatman No. 42 filter paper before AAS analysis. Silicon and Al analyses were conducted using a mixed acetylene-nitrous oxide flame. Organic C extracted by pyrophosphate (Cp) was measured on a Phoenix 8000 UV Persulfate TOC Analyzer (Tekmar-Dohrmann, Cincinnati, OH).
Thin sections of rocks from the AN parent material were prepared from rock fragments embedded in Petropoxy and ground to 30-µm thickness. Visual analysis of thin sections were made with a petrographic microscope (Olympus BH2, Olympic Industrial America Inc., Orangeburg, NY)
Carbon Distribution in Density and Aggregate Fractions
We analyzed three morphological horizons (A2, Bt1, and BC) of each pedon for C distribution in density and aggregate fractions. The selected horizons represent similar depths and morphologic horizons in each parent material, and provide a range of depths and properties that may be used to characterize C and aggregate characteristics for the entire pedon. Methods used for aggregate fraction separation are similar to those of Golchin et al. (1994) and Sohi et al. (2001).
In 250-mL polycarbonate centrifuge bottles, 30 g of soil was mixed with 150-mL of sodium polytungstate (SPT) at a density of 1.6 g cm–3, and allowed to settle for 20 min. Samples were then centrifuged for 10 min at 1180 x g. Light fraction material was removed by aspirating the supernatant and vacuum filtering over 0.8-µm polycarbonate filters to collect this "free" light fraction material on the filter. The mixing and free light fraction removal was repeated three times or until no light fraction material remained after settling. Free light fraction material was washed thoroughly on the filter with deionized (DI) H2O, collected in beakers, and dried at 50°C. The heavy fraction remaining after centrifugation was resuspended in SPT and treated with ultrasonic energy (Branson Sonifier 450, Branson Ultrasonics, Danbury, CT) of 1500 J (g soil)–1 over a 5-min period, according to Sohi et al. (2001). This treatment presumably releases non-mineral associated free organic matter "occluded" within aggregate structures. The ultrasonic probe tip was inserted 5-cm below the liquid surface during disruption. The rate of energy output was calibrated by measuring the change in temperature of 100-mL of DI H2O after a 5-min treatment with ultrasonic energy (North, 1976). Occluded light fraction released after ultrasonic dispersion was collected following the methods described above. The remaining heavy "mineral" fraction was repeatedly rinsed by shaking with DI H2O, centrifuging at 9715 x g for 30 min, and decanting the supernatant to wash the mineral fraction free of SPT. This was repeated three times, followed by drying at 50°C. The three resulting fractions are referred to as "free," "occluded," and "mineral."
Total organic C, N, and 13C were measured in each horizon and aggregate fraction using a combination of high temperature dry combustion (Carlo-Erba Elemental Analyzer, CE Elantech, Inc.), and continuous flow Isotope Ratio Mass Spectrometry (Europa Hydra 20/20, PDZ Europa, Cheshire UK). Soils did not react with HCl, and therefore were not pretreated to remove carbonates before C analyses.
Aggregate Stability
Ultrasonic dispersion was used to quantify aggregate stability following procedures modified from Fuller and Goh (1992). Soil from the A2, Bt1, and BC horizon of each pedon were slowly wetted over a 30-min period with repeated spray of DI H2O. Samples were then mixed to a 1:10 soil/water ratio and treated with four levels of ultrasonic energy: 0, 160, 750, and 1500 J (g soil)–1. For the 0-J treatment, samples were briefly shaken (<30 s) with DI H2O. After disruption, samples were gently wet sieved (using spray from a water bottle) at 53 µm and clay and silt collected in 1-L graduated cylinders. Clay was then measured by pipette. The energy treatments were not sequential; a fresh soil sample was used for each energy treatment. The clay released at each energy level relative to the clay released at 1500 J (g soil)–1 provides an index of aggregate stability, with an inverse relationship between the percentage of clay released and aggregate stability. Preliminary analysis indicated that clay released at 1500 J (g soil)–1 is roughly equivalent to clay released by traditional PSA [e.g., 90–100% of PSA clay recovered by 1500 J (g soil)–1 treatment; data not shown].
Radiocarbon Analysis of Aggregate Fractions
The radiocarbon content of the density and aggregate fractions (free, occluded, and mineral) from the A2, Bt1, and BC horizons was determined by Accelerator Mass Spectrometry (AMS) at Lawrence Livermore National Laboratory. For each horizon, density and aggregate fractions from the three pedons per stand were composited for AMS analysis. Graphite targets were made by complete combustion of soil fractions to CO2 that was then purified cryogenically and reduced to graphite by sealed-tube zinc-reduction (Vogel, 1992). Analytical precision of 
14C data was better than ± 6
.
Statistics
Pedons in each stand were treated as replicates for each parent material. Every horizon of each pedon was analyzed for physical and chemical properties (except for XRD that was performed only on horizons from the central pedon), with presented horizon values representing an average for all three pedons in a stand. As noted above, radiocarbon analyses were performed on composited density and aggregate fractions, so there is only one replicate for each horizon and aggregate fraction by parent material. Weight percentage values were converted to a kg m–2 basis using bulk density values and corrected for coarse fragment content (USDA, 1996). Mass per area values from each horizon were then summed by pedon. Significance of pedon sums between stands was tested using a one-way ANOVA model, and means compared using a t test and pairwise comparison. Linear regression analysis between mineral variables and soil C content (on a kg m–2 basis) was used to correlate physical and chemical data to soil C content. Granite and AN pedons were pooled for regression analysis (n = 6; three pedons from each stand). All analyses were performed using JMPIN v.5.1 (SAS Institute Inc., Cary, NC).
|
RESULTS AND DISCUSSION |
|---|
|
TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
|
Soil Mineral Assemblage
Thin section analysis of rocks from the AN parent material (micrographs not shown) reveal that some of the parent rock is a mix of biotite, feldspar, quartz, and pyroxenes embedded in a fine grained matrix, suggesting a fine-grained granodiorite composition. Andesite cobbles were also identified in the AN stands. It appears that the parent material of this stand is a mix of andesitic and granitic material. This mix of materials provides a soil with very similar crystalline mineral species to those of the GR soils, but one that differs in SRO mineral and Al-humus complex content, with the andesite parent material contributing to greater Al- and Fe-oxy-hydroxide content (Table 2).
|
|
Selective Dissolution
The similarity in crystalline mineral species allows for comparison of the effects of varying sesquioxide, SRO alumino-silicate, hydroxy-Al (Al-OH), and hydroxy-Si (Si-OH) materials, and Al-humus complex content, as determined by selective dissolution procedures, on soil C dynamics (Table 2). Both soils have low amounts of SRO alumino-silicates as evidenced by low Sio content and high (Alo–Alp)/Sio molar ratios. The high ratios suggest that the majority of the SRO Al derives from non-crystalline Al-OH species or from HIV interlayer Al species (Southard and Southard, 1989; Dahlgren and Saigusa, 1994). Crystalline Fe-oxide content increases with depth in both soils, particularly in the Bt and BC horizons, but AN soils have nearly double the amount of Fe-oxides relative to GR soils. Greater Fe-oxide content in the AN soils is likely a function of the mafic andesite parent material. The dominance of crystalline Fe-oxide species relative to SRO species (Feo), such as ferrihydrite, also suggests a zone of high weathering intensity and frequent wet dry cycles (Schwertmann and Taylor, 1989). The Ald, Alp, and Cp content also increase with depth, reaching a maximum in Bt1 horizons, and are significantly greater in AN soils. Ald may come from Al substituted into Fe-oxyhydroxides or from HIV interlayers (Parfitt and Childs, 1988). Andesite-granite soils show interlayering of vermiculite clays in Bt and BC horizons (based on XRD), which may account for the significantly greater Ald. In addition, Ald may also be sourced from SRO minerals, as citrate is an effective dissolution agent for poorly crystalline minerals (Parfitt and Childs, 1988).
The accumulation of Alp in Bt horizons and relatively low content in A horizons suggests a movement of Al-humus complexes from surface to subsurface horizons. Alp/Cp molar ratios increase with depth in AN soils, while the Alp/Cp ratio peaks in the Bt of GR soils, suggesting precipitation of insoluble Al-humus complexes or colloidal Al-OH complexes in Bt and BC horizons. Alp/Cp molar ratios greater than 0.1 correspond to decreased Al-humus mobility and increased Al-humus complex precipitation (Boudot et al., 1989; Schwesig et al., 2003). Higashi (1983) suggested a maximum complexing capacity for synthetic humic substances of 0.12–0.22 for Alp/Cp molar ratios, with greater ratios suggesting extraction of Al from sources other than Al-humus complexes. Using this range as a guide, our Alp/Cp values suggest saturation or near saturation of C with Al in all horizons, particularly AN subsurface horizons. The additional extracted Alp may derive from Al in interlayer positions or other relatively labile forms of surface-precipitated Al (Dahlgren and Walker, 1993). The saturation of soil C with Al species may affect both organomineral association and soil C biodegradability. Aluminum complexation will condense the conformation of humic substances such that greater C may approach and adsorb to mineral surfaces, possibly decreasing biodegradation from enhanced physical protection (Theng, 1979), while Al saturation may also impart chemical recalcitrance due to Al toxicity to microbes (Illmer et al., 2003).
The proportion of total C extracted by sodium pyrophosphate (Cp/C) increased with depth in both soils. Sodium pyrophosphate extracts C in metal-humus complexes as well as weak-base soluble soil C species (Stevenson, 1994). The decreasing Alp and increasing Cp/C in BC horizons suggest subsurface Cp contains a greater proportion of weak-base soluble C species rather than metal-humus complexes. Increasing Cp/C with depth indicates transport of low molecular weight "fulvic acids" from surface to subsurface horizons. This pattern of translocation and precipitation/mineral adsorption of low molecular weight acids (part of the podzolization process) is commonly observed in Spodosols (Buol et al., 2003) and may represent an important mechanism for subsurface protection of organic matter, even in these soils that don't have obvious morphological evidence of podzolization. Indeed, podzolization processes were also indicated as a significant factor in soil C storage and stabilization in grassland soils, exemplifying the potential impact of podzolization on soil C cycling in soils other than Spodosols (Masiello et al., 2004).
Aggregate Stability
Aggregate stability exhibited similar patterns in AN and GR soils (Fig. 2)
, with greater aggregate stability in A horizons relative to subsurface horizons. A two compartment exponential growth model gave the best fit to the percentage of clay released at each energy treatment relative to the clay released at the 1500 J (g soil)–1 treatment (Fig. 2). The two compartment model represents two pools of aggregates with different stability. Model parameters (a) and (c) represent pool size in units of % clay released, while parameters (b) and (d) are constants for each pool in units of [J (g soil)–1]–1. The stability of the aggregate pool may be estimated by the inverse of the exponential constant, estimating the J (g soil)–1 required to disaggregate the aggregate structures in that pool. Granite and AN soils had very similar aggregate pool size (model components a and c) and similar stability indices (1/b and 1/d). The less stable pool required from 103 to 145 J (g soil)–1 for disruption, while the stable pool required roughly 1000 J (g soil)–1. The exception is the A2 horizon of the AN soils, that showed a modeled stable pool stability index of 2500 J (g soil)–1, suggesting that this pool was not completely disaggregated with the 1500 J (g soil)–1 treatment. Both AN and GR soils exhibited an increase in the less stable pool and decrease in stable aggregate pool size with depth, suggesting the importance of surface organic matter input to stable aggregate pool dynamics.
|
|
Several trends are apparent in density and aggregate fraction C with radiocarbon analysis (Fig. 3)
. Overall 14C content decreases with depth, suggesting older C with depth. Free fraction material is the most enriched 14C material in all horizons in both parent materials, suggesting a "young" C pool; occluded C fractions exhibit the greatest 14C depletion, suggesting an "old" C pool; mineral fractions show intermediate 14C values. For each horizon, the free and mineral AN fractions were older than comparable GR fractions.
|
It is possible that the very old occluded C fraction in the AN Bt horizon contains a significant portion of C in the form of charcoal. For example, Kahle et al. (2003) found a high correlation between C MRT in coarse clay fractions and condensed aromatic ring structures that suggested the presence of charred organic materials. Subsurface charcoal deposits were observed in the field, and appeared to occupy old root channels. The presence of charcoal was also confirmed by visual inspection of the free fraction of both AN and GR soils. It is possible that the burn history of the two stands differs and that the AN soils received significant input from wildfires several thousand years before present (based on the 14C content of the occluded Bt C). It is also possible the AN mineral assemblage is more effective at charcoal stabilization than that of the GR soils, with possible interactions between SRO minerals, charcoal, and aggregate formation. However, it is unclear why only the occluded C in the AN Bt horizon shows such a depleted 14C signature.
Free and mineral fractions show greater radiocarbon age in the AN soils, and the greatest age separation between parent materials in each horizon. Greater Al-humus complex and SRO Al mineral content in AN soils may promote mineral association of organic molecules, thereby enhancing the chemical and physical protection of mineral associated C in the AN soils. Mineral C consists of relatively highly decomposed material (according to C/N and 13C data), but exhibits a relatively old radiocarbon age, suggesting that mineral association promotes stabilization of humic substances (e.g., Balesdent, 1996).
Regression Analysis
Regression analysis of total C content with soil mineral variables suggests that Al-humus complexes and SRO Al minerals account for the majority of the variance in soil C content (Table 4). Except for the A1 horizon, which did not show a significant relationship to any of the mineral variables, Al species explain from 80 to 99% of the variation in C content for each horizon. We hypothesize that Al-humus complexes precipitate in A2 horizons, as suggested by an increase in Alp/Cp ratios. These organomineral precipitates effectively protect soil C from decomposition (Boudot, 1992) and possibly act as a "glue" to bind soil particles together, thereby promoting aggregation and occlusion of organic materials. Aluminum-humus complexation in BC horizons may facilitate greater organomineral binding to existing clay minerals through cation bridging mechanisms. Aluminum-humus complex content is much greater in the subsurface of AN soils and corresponds to greater soil C content in subsurface horizons relative to GR soils. The re-emergence of Alp as an important parameter in the BC horizons may be a function of the podzolization process where a certain percentage of mobile Al-humus complexes are leached into subsurface horizons. These subsurface Al-humus complexes may be sourced from either A or Bt horizons and consist of microbial byproducts or partially decomposed organic matter.
|
Soil Carbon Pool Size and Mean Regression Time
Using the percentage of total horizon C (on a kg m–2 basis) that each fraction represents and the estimated 14C age of each fraction, the relative proportion of fast and slow cycling pools may be determined. For A2 horizons, nearly 80% of the C in both the GR and AN soils is fast cycling C (MRT < 100 yr). Trumbore et al. (1996) also found that 50 to 90% of soil C in the upper 20 cm of forest soils on granite parent materials has rapid turnover rates (7–65 yr). Twenty percent of AN and GR A2 soil C is within the occluded fractions that possess relatively long MRT (>150 yr), suggesting that the majority of C protection comes from occlusion within aggregate structures in this horizon.
The Bt1 horizons exhibit significant deviation in the proportion of fast and slow cycling C between AN and GR soils. All of the AN fractions have MRT's greater than 150 yr, with approximately 80% of the soil C having a MRT of greater than 400 yr. In contrast, the GR Bt1 horizon has roughly 30% of its soil C in fast cycling pools with modern 14C signatures. The largest difference in C content in this horizon between stands is in the mineral fractions, with AN soils having nearly three times as much mineral associated C. The greater mineral C association may be related to the SRO mineral content, in particular Alo as suggested by regression analysis.
In BC horizons, all soil C fractions have relatively long MRT, with no significant portion of fast cycling C. The AN free and mineral fractions have longer MRT's than GR free and mineral fractions, that is probably due to Al-humus complexation, as suggested by regression analyses.
|
CONCLUSIONS |
|---|
|
TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
Received for publication February 2, 2005.
|
REFERENCES |
|---|
|
TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
This article has been cited by other articles:
|
|
 |
|
  D. Solomon, J. Lehmann, J. Kinyangi, B. Liang, K. Heymann, L. Dathe, K. Hanley, S. Wirick, and C. Jacobsen Carbon (1s) NEXAFS Spectroscopy of Biogeochemically Relevant Reference Organic Compounds Soil Sci. Soc. Am. J., September 11, 2009; 73(6): 1817 - 1830. [Abstract] [Full Text] [PDF]
|
|
|
|
|
|
C. Rasmussen, R. J. Southard, and W. R. Horwath Soil Mineralogy Affects Conifer Forest Soil Carbon Source Utilization and Microbial Priming Soil Sci. Soc. Am. J., June 8, 2007; 71(4): 1141 - 1150. [Abstract] [Full Text] [PDF]
|
|
|
|
|
|
C. Rasmussen, N. Matsuyama, R. A. Dahlgren, R. J. Southard, and N. Brauer Soil Genesis and Mineral Transformation Across an Environmental Gradient on Andesitic Lahar Soil Sci. Soc. Am. J., January 1, 2007; 71(1): 225 - 237. [Abstract] [Full Text] [PDF]
|
|
| ||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||
| HOME | HELP | FEEDBACK | SUBSCRIPTIONS | ARCHIVE | SEARCH | TABLE OF CONTENTS |
| The SCI Journals | Agronomy Journal | Crop Science | |||
| Journal of Natural Resources and Life Sciences Education |
Vadose Zone Journal | ||||
| Journal of Plant Registrations | Journal of Environmental Quality |
The Plant Genome | |||
