Login   /   Register
Di Bene, Marchetti, Francaviglia, and Farina: Soil Organic Carbon Dynamics in Typical Durum Wheat-Based Crop Rotations of Southern Italy

Soil Organic Carbon Dynamics in Typical Durum Wheat-Based Crop Rotations of Southern Italy


Mediterranean agricultural areas are dominated by cropping systems based on winter cereals crops, summer irrigated crops, foragebased systems, and mixed succession with bare fallow. Soil organic carbon (SOC) is widely used to assess the environmental performance of these cropping systems, since it is strongly influenced by management practices and environmental conditions. This study evaluates the sustainability of representative intensive cropping systems of Southern Italy, in terms of SOC stock changes and CO2 emissions in the long-term perspective, using a process-based model (RothC10N) combined with a GIS-based spatialization procedure. On the basis of SOC modelling, results showed that crop management practices currently adopted by farmers did not guarantee SOC sequestration in all the rotations (–4.29 Mg C ha–1). The sustainability of cropping systems can be improved through management practices such as the retention of crop residues into the field and/or the rational use of irrigation for the summer crop (6.73 Mg C ha–1). This finding could help policy makers to provide suggestions for a more effective local implementation of agro-environmental measures.


In the last decades, Mediterranean cropping systems have undergone strong variations due to the intensification of agricultural activities in the most productive plains (Serra et al., 2008), and the extensification of land uses in less fertile zones (Bindi and Olesen, 2011; Nainggolan et al., 2012). Frequently, these changes may cause a simplification of agricultural production systems with significant consequences on environmental impacts and agroecosystem services. It is well-established that in conventional agronomic schemes, unsuitable agricultural practices, such as deep tillage, reduction in crop rotation length, and the removal of crop residues may have negative implications on soil organic carbon (SOC) pool (Le Gal et al., 2010; Álvaro-Fuentes et al., 2011; Martiniello, 2011; Pisante, 2013). So far, semi-arid areas of Southern Italy are dominated by cropping systems mostly oriented on winter cereals-based rotations, such as continuous durum wheat (Triticum durum Desf.), durum wheat-summer irrigated crops, forage-based systems, and mixed succession with bare fallow (Borrelli et al., 2011; Martiniello, 2011). In these agroecosystems, SOC level is quite low due to soil degradation processes. Thus, conservative farmlands can act as potential C sink, although the possibilities of SOC sequestration are quite site specific and strongly influenced by soil management and environmental factors (VandenBygaart et al., 2002; Rodríguez Martín et al., 2016). SOC is normally considered an indicator of soil quality, and soil can accumulate C for decades (Ruiz Sinoga et al., 2012). It is widely known the crucial role of SOC to maintain soil fertility, crop production potential, and prevent soil quality deterioration thanks to its filtering and buffering capacity (Kirchmann and Andersson, 2001). However, the studies of SOC dynamics based on field experiments and local surveys are costly and time consuming. Alternatively, many process-oriented models are available for predicting SOC dynamics on a temporal and spatial basis, with the most frequently adopted being Century (Parton et al., 1987), RothC (Jenkinson and Rayner, 1977; Jenkinson, 1990) and its recent modified version RothC10N (Farina et al., 2013).

The study aimed to propose a methodology to predict temporal SOC stock changes between 1994 and 2013 in representative intensive cropping systems of Southern Italy, using a process-based modelling approach and a GIS-based spatialization procedure. The purposes of the paper deal with: i) evaluating temporal and spatial SOC stock variations affected by current crop management using RothC10N model; and ii) understanding the factors influencing SOC maintenance in order to propose alternative management practices to improve soil C sequestration and reduce CO2 emissions to be implemented in the local agro-environmental policies.

Materials and methods

Study area

The study was conducted in the Manfredonia Municipality, located in the Southeast part of the Capitanata plain, Apulia Region, Southern Italy (Figure 1). The area, with an elevation between 0 and 604 m a.s.l., was selected as pilot study because of its importance in the Italian agriculture context, mostly for the production of winter durum wheat and tomato. The utilised agricultural area (UAA) covers 282.25 km2, almost 80% of the total area after the 2010 agricultural census (ISTAT, 2010). Land use is based on intensive agriculture, characterised by the cultivation of rainfed winter cereals (mainly durum wheat; 54.78%), irrigated summer horticultural crops (mostly tomato; 13.25%), forage and pasture systems (17.11%), olive trees and vineyards (5.48%). Livestock farms in Manfredonia accounts for less than 1% of the total in Apulia Region, and are mostly based on cattle and buffaloes (44%) and sheep and goats (38%). Climate is classified as Cfa (warm temperate, fully humid, hot summer) according to the updated Köppen-Geiger climate classification (Kottek et al., 2006). Long-term annual average temperature is 15°C, while average annual rainfall ranged from 684 to 730 mm, mostly concentrated in the autumn-winter months. Typically, soils are deep with a clay (86%), silty-clay (13%) or clay-loam (1%) texture, and are classified (WRB, 2014) as Vertisols (42%), Phaenozems (25%), Luvisols (21%), Arenosols (4%), Calcisols (4%), Kastenozems (4%), and Leptosols (4%).

Overall methodology

In this study, we propose a methodology to predict SOC stock changes in arable cropping systems and pastures across the Manfredonia Municipality, using a process-based modelling approach and a GIS-based spatialization procedure as follows: i) harmonise and combine weather, soil, and crop succession data, in a unique spatially explicit dataset in a GIS environment; ii) run the SOC model in batch mode that routinely takes inputs from the unique spatially explicit database and writes outputs to the same database; iii) analyse the predicted variation in SOC stock considering the current (baseline) and three alternative management scenarios for the main cropping systems studied.

Data sources

Weather database: For the 1989-2013 time period, mean monthly rainfall, temperature, and evapotranspiration data were extracted for the closest grid (20 × 20 km) from the AGRI4CAST archive (http://mars.jrc.ec.europa.eu/mars/About-us/AGRI4CAST), and validated with locally observed data. Weather data were downscaled at field level following the geographically weighted regression method as described in Fotheringham et al. (2003) and then formatted to be stacked into the GIS.

Soil database: A georeferenced soil database covering the entire Manfredonia Municipality (354.54 km2) was obtained as a subset of the georeferenced soil database of Foggia Province by clipping the Manfredonia boundaries. The whole database includes 280 soil profiles from the CREA-RPS repository, described by the main soil physical (texture, bulk density, hydrological constants) and chemical properties (pH, CEC, soil organic carbon and total nitrogen concentrations). All soil data were normalised over the 0-30-cm layer for the modelling. Empirical Bayesian Kriging of the soil profiles was used as spatialization procedure to predict the value of SOC, clay and silt parameters in not sampled points (Figure 2).

Crop succession database: A georeferenced crop succession database for the 1994-2013 period was obtained by the collation and harmonisation of the following data sources: i) AGRIT database: is part of the sample survey project performed by Italian Ministry of Agricultural, Food and Forestry Policies (MIPAAF) since 1988, based on a point frame sampling land parcel cover survey, over all the Italian territory. The database was used to define the georeferenced crop succession in Manfredonia for 1994-2013 period (234 annual records) (Figure 1); ii) FADN-RICA database: Italian Farm Accountancy Data Network - Rete di Informazione Contabile Agricola (FADN-RICA, http://rica/public/it/index.php) concerning yearly economic information of farms, reporting UAA, utilised irrigated area, crop rotations and crop yields. The database was used to estimate crop yields and C inputs to the soil based on farms crop yield data. Sixteen most representative farms of the Manfredonia agricultural systems were monitored from 2001 to 2012 period; iii) Corine Land Cover (CLC) datasets: The land use and land cover of Manfredonia was defined considering the following agricultural area categories: arable land (non-irrigated and permanently irrigated) and pastures (source: http://uls.eionet.europa.eu/CLC2006/CLC_Legeng.pdf).

Spatial interpolation database

Harmonised spatially explicit weather and soil database were intersected with crop succession database using a spatial overlapping procedure in a GIS environment. After this procedure, a specific and geo-referenced value of weather and soil parameters was assigned to each crop succession record. This unique combined dataset was used to setup all input files (e.g., weather and land management) for running the model to an equilibrium state (initialisation), and in batch mode for the long-term SOC simulations (1994-2013) of all dataset crop succession records.

Crop management practices and estimation of carbon input to soil

As reported in previous studies carried out in the Capitanata plain, continuous rainfed winter cereals [mainly durum wheat (DW); Triticum durum Desf.] and durum wheat in rotation with irrigated summer crops [mainly processing tomato (T); Solanum lycopersicum L. ] are the most common crop rotations. Cropping systems frequently include one year of fallow, and organic fertilisers are not applied to arable crops (Borrelli et al., 2011; Farina et al., 2013). Table 1 shows the main agronomic practices, currently used by farmers for durum wheat and tomato crops. Soil C input is mainly derived from crop materials. During bare fallow (BF), the soil cover biomass (composed by spontaneous species) is totally incorporated into the soil with tillage. Carbon inputs used for modelling were calculated from crop yield and from bibliographic sources as reported in Table 2. As detailed in Farina et al. (2013), plant C inputs were estimated as the sum of C inputs from crop residues (Cr), roots (Crot), root exudates (Ce), and weeds (Cw). In the study area, crop residues were commonly removed from the field. We estimated that C from Cr incorporated into the soil was 10-15% of the total aboveground biomass dry matter, and root C inputs as 10-15% of the harvested aboveground biomass according to Skjemstad et al. (2004). Rhizodeposits were calculated following Bolinder et al. (2007) procedure, and we assumed that root exudates were 9% of the total aboveground biomass dry matter as given by Kuzyakov and Domanski (2000). Carbon inputs from weeds were estimated to be 7-15% of total aboveground biomass dry matter. Biomass dry matter was converted to C assuming a carbon content of 45% (Johnson et al., 2006).

The C input values calculated for each crop were fitted with the average C input values estimated running the model in inverse at equilibrium for the 234 crop succession records considered. The model outputs also predict how much C should be returned to the soil to maintain the initial SOC stock.

Model description

In the present study, we used the RothC10N model, a modified version of the original RothC model (Coleman and Jenkinson, 1996; Jenkinson et al., 1999) by Farina et al. (2013), allowing to bettersimulating SOC dynamics under semi-arid and Mediterranean conditions (Figure 3). This is a process-based, multi-compartmental SOC turnover model, which simulates the effect of soil type, temperature, soil moisture content and plant cover on the turnover process. The model splits SOC inputs into one inert organic matter pool and four active compartments named: decomposable plant material (DPM), resistant plant material (RPM), microbial biomass (BIO) and humified organic matter (HUM). Each of the active pools decomposes by first order kinetics into CO2, BIO and HUM. Decomposition of each pool is influenced by air temperature, soil moisture, and plant cover (Figure 3). The model uses a monthly time steps to calculate total SOC and its different pools on a years to centuries time scale. It requires few easily obtainable input parameters, and produces reliable and accurate simulations with a good general performance (Falloon and Smith, 2002; Guo et al., 2007; Ludwig et al., 2010; Francaviglia et al., 2012). At the end of the simulation, RothC10N predicts total SOC storage along with its different compartments and evolved CO2. The data needed to run RothC10N were:

Climate data: Monthly rainfall (mm), monthly open pan evaporation (mm), average monthly mean air temperature (°C);

Soil data: Clay and silt content (%), initial SOC stock (Mg C ha-1), bulk density (Mg cm–3), depth of the soil layer considered (cm), field capacity (mm), wilting point (mm), hygroscopic water content (mm);

Land use and land management data: Soil cover, monthly input of plant residues (Mg C ha–1), monthly input of farmyard manure or any other organic fertiliser (Mg C ha–1), residue quality factor (DPM/RPM ratio, an estimate of residue decomposability according to the vegetation type). We set DPM/RPM ratio to 1.44 for all crops considered. Irrigation management is not a module of RothC model, thus, in irrigated systems, weather file must be modified by adding the irrigation water used for crops to the monthly rainfall amount (rainfall + irrigation) occurred during irrigated crop periods. Irrigation amount added to monthly rainfall was assumed equal to the soil water deficit (pan evaporation-rainfall).

Management scenarios

In the present study, SOC stock changes were predicted by RothC10N model for the 1994-2013 period, considering the commonly agronomic practices adopted by farmers. The current crop management was taken as the baseline (S0) and three alternative scenarios where identified in order to increase C sequestration in soil. S0 for arable crop (AC) land use category was run considering 15% of arable crop residues left in the field and irrigation refilling to 100% of soil water deficit. Alternative management options could either act to decrease C losses or to increase C inputs. The first scenario (S1) was run considering management practices directly linked to the increase in C input in AC land use category by the incorporation of crop residues, and the improvement of semi-natural pasture in pasture (GL) land use category by overseeding leguminous as mixture and by a proper phosphorus fertilisation. The other two scenarios (S2 and S3) focused on irrigated crop sequences (ACi) and were run taking into account the management of crop residue and a more efficient and sustainable use of water in irrigation. Scenarios are defined as follows: i) S1: In arable crops, 100% of residues are incorporated to soil and irrigation as in S0; pastures are improved to increase plant cover and productivity; ii) S2: Leave 15% of arable crop residues in the field and reduce summer crop irrigation volume to 50% of the soil water deficit, for irrigated-based cropping systems; iii) S3: Leave 100% of arable crop residues in the field and reduce summer crop irrigation volume to 50% of the soil water deficit, for irrigated-based cropping systems.

These alternative practices could represent possible options for farmers for a more sustainable crop management, reducing the soil organic carbon loss.

Results and discussion

Description of the local cropping systems

According to the CORINE land cover classification, the 234 georeferenced 20-year crop successions were aggregated into two macro classes: AC and GL. AC rotation includes rainfed and irrigated cropping systems, mostly dominated by the rotation with DW. Based on AGRIT 1994-2013 database, in 41% of crop succession units, DW was cultivated in continuous, while in 43% was cultivated in rotation with BF (13%), or with processing T (18%) or with both BF and T (12%). GL covers 17% of total crop succession units and includes semi-natural pastures mostly based on spontaneous herbaceous vegetation and meadows. More details on crop sequences are reported in Table 3.

One of the main strength of this study is the use of the annual crop succession georeferenced database as model input. This permits to obtain good predictions of SOC dynamics for the different cropping systems, and to evaluate which crop rotations could favour C sequestration.

Initial soil organic carbon stock and stock variations, and CO2 emissions (1994-2013)

Initial SOC stock associated to each crop succession unit was obtained by overlaying the crop succession database to the spatialized soil database. The majority of crop succession units were in Vertisols and Luvisols (90%) with a prevalent clay soil texture (85%). The estimated value of initial SOC stock was on average 45.97 Mg C ha–1, ranging between 44.79 and 49.54 Mg C ha–1 in continuous DW and GL, respectively. Table 3 reports details on initial SOC stock for the land use categories studied. Final SOC stock in each crop succession units was predicted by RothC10N for the baseline (S0) and the three alternative management scenarios (S1, S2, S3) after 20 years of simulations. The model has been tested for the first time by Farina et al. in 2013 in similar cropping sequences and pedo-climatic conditions, using data from a long-term field experiment carried out at CREA-CER farm in Foggia Province. The authors reported that the difference between measured and modelled SOC was 0.11 Mg ha1 yr–1 with a root mean standard error value of 3.4%. These results confirm that RothC10N model provided fair SOC stock simulations in these environments, especially for rotations that included BF. Irrespective of soil type, the values ranged from 40.25 Mg C ha–1 (in ACi land use category with BF in rotation) to 45.13 Mg C ha–1 (under continuous DW) in scenario S0, and from 47.01 Mg C ha–1 (under ACi with BF) to 56.83 Mg C ha–1 (in continuous DW) in scenario Si. S2 and S3 scenarios considered changes in management only for ACi land use category, namely a reduction in irrigation amount and an increase of C inputs coupled with irrigation reduction, respectively. On average, SOC stock increased by 4% in S2 and 25% in S3 with respect to the initial SOC stock. Maximum percentage of SOC increases with respect to S0 was found for S1 and S3, with 20% and 40% respectively. Results allowed to derive the SOC sequestration rates of the four scenarios arising from the model predictions, and expressed in Mg C ha–1 yr–1. Over the 20-yrs period, S0 showed a negative SOC sequestration in all the rotations including bare fallow and/or tomato (-0.21 Mg C ha–1 yr–1) and a positive value with continuous DW (0.02 Mg C ha–1 yr–1) that can be considered in a steady-state condition. The highest loss of SOC was observed in GL and ACi land use categories with a mean decrease of 12% (Table 3). Final SOC predicted for the baseline in the GL land category suggests that poor management practices are important human-controlled factors that strongly influence pasture production and cause the depletion of soil carbon stocks (Ojima et al., 1993; Conant and Paustian, 2002). Our negative findings obtained for GL land category in the baseline are in contrast with the values reported in other Mediterranean systems (Francaviglia et al., 2014). However, improving grassland management can potentially reverse historical soil carbon losses and sequester substantial amounts of carbon in soils. Increasing production, maximize vegetative cover, carbon inputs or below-ground allocation, could increase SOC stocks (Conant et al., 2001; Follett et al., 2001). Moreover, final SOC predicted for the baseline management in the ACi land use category, showed that rotations including irrigated summer crops favour the degradation of soil C due to the combination of water availability and high temperatures. In the S1, S2 and S3 alternative management scenarios, SOC sequestration rates were always positive, ranging from a maximum of 0.64 Mg C ha–1 yr–1 in S3 for the 3-years durum wheat-tomato rotation, to a minimum of 0.07 Mg C ha–1 yr–1 in S2 for the durum wheat in rotation with tomato and bare fallow. Predicted SOC in the different scenarios pointed out the patterns of potential SOC loss reduction due to the alternative crop management practices applied in all land use categories. In the present study, all alternative scenarios increased SOC stock compared to the baseline. As regards SOC stock predicted considering 100% of crop residue incorporation strategy for arable crops (S1), our positive results are consistent with Bakht et al. (2009) study, reporting a mean annual increase in SOC value 1.04 times greater in the residues retained than removed treatment. Several study carried out worldwide confirm that leaving crop residues in the field after harvest is one way to stabilise soil fertility (Convertini et al., 1998; Franzluebbers, 2002; Lemke et al., 2010). However, the increase in SOC stock derived from this process is strongly affected by pedo-climactic features, type of crop residue, and agronomical practices adopted. As regards SOC stock in the improved pasture (S1), our results are in good agreement with Gonzalez and Candás (2004), and Francaviglia et al. (2014) reporting values of 54 Mg C ha–1. The higher SOC stock predicted in S1 for GL land use category with respect to the baseline (S0) can be ascribed to the improvement of floristic composition, plant density obtained after overseeding pasture with leguminous mixture. In fact, sowing more productive species and/or supplying adequate nutrients, result in greater forage production (Nash et al., 2014) and carbon stocks (Conant et al., 2001).

Table 4 reports the twenty-years cumulated CO2 emissions predicted by RothC10N model. CO2 emissions were on average 171.45 Mg CO2 ha–1 in the baseline. The highest emissions were predicted for ACi crop sequences (199.54 Mg CO2 ha–1) and the lowest for grasslands (123.09 Mg CO2 ha–1). The long-term predictions suggest that the most effective land use category considering both SOC sequestration and CO2 emissions was ACi when incorporation of crop residues and a rational use of irrigation water were adopted. In details, S2 and S3 land management scenarios show that the tomato residues returning on the soil increased the biomass useful for humification processes. Also, these scenarios pointed out that in the semi-arid environments typical of southern Italy where evapotranspiration during summer is higher than rainfalls, the use of water resources for irrigation is a priority that should be managed considering a sustainable regulation of water deficit, which can contribute to save water with environmental and economic benefits (Zornoza et al., 2016), but without affecting crop productivity (Campi et al., 2014; Giuliani et al., 2016) so to maintain the profit for farmers. In fact, Leogrande et al. (2012) investigated the rational use of water resources and observed that the reduction of irrigation volume to 50% of crop water requirements did not significantly affect soil chemistry and tomato yield and quality in similar pedo-climatic conditions. Another important strategy to increase C inputs in intensive durum wheat-tomato rotation includes the use of cover crops during the winter season, after wheat and before tomato, that could be either used as green manure or flattened, with positive effect also on the weeds and in the build-up of C stocks (Canali et al., 2013).


The methodology proposed in this study to predict SOC stock changes has shown a good ability to characterise the existing cropping systems in the study area, and to understand the dynamics currently acting. RothC10N model is a suitable tool for assessing at regional level the sustainability of cropping systems in terms of SOC stock changes and CO2 emissions in the long-term. Results showed that on the basis of SOC modelling, the sustainability of cropping systems could be improved through alternative management practices. In the most intensive cropping system, based on durum wheat-tomato crop rotation, the adoption of practices such as the retention of crop residues into the field and the rational use of irrigation can result in a substantial and positive change in SOC stock in comparison with the current management. Both practices are effective to improve SOC sequestration and maintain the profits for farmers. Results could also provide indications for policy makers to implement effective agro-environmental measures, and for valuing soil C sequestration in the carbon-credit market.



J Álvaro-Fuentes, M Easter, C Cantero-Martinez, K Paustinan, 2011. Modelling soil organic carbon stocks and their changes in the North-East of Spain. Eur. J. Soil Sci. 62:685-95.


J Bakht, M Shafi, MT Jan, Z Shah, 2009. Influence of crop residue management, cropping system and N fertilizer on soil N and C dynamics and sustainable wheat (Triticum aestivum L.) production. Soil Till. Res. 104:233-240.


M Bindi, JE Olesen, 2011. The responses of agriculture in Europe to climate change. Reg. Environ. Change 11:151-8.


MA Bolinder, HH Janzen, EG Gregorich, DA Angers, AJ VandenBygaart, 2007. An approach for estimating net primary productivity and annual carbon inputs to soil for common agricultural crops in Canada. Agric. Ecosyst. Environ. 118:29-42.


L Borrelli, S Colecchia, A Troccoli, S Caradonna, R Papini, D Ventrella, MT Dell’Abate, C Galeffi, C Tomasoni, R Farina, 2011. Effectiveness of the GAEC standard of cross compliance crop rotations in maintaining organic matter levels in soils. Ital. J. Agron. 6:57-62.


P Campi, F Modugno, M Mastrorilli, F Tomei, G Villani, V Marletto, 2014. Evapotranspiration of tomato simulated with the CRITERIA model. Ital. J. Agron. 9:93-8.


S Canali, G Campanelli, C Ciaccia, F Leteo, E Testani, F Montemurro, 2013. Conservation tillage strategy based on the roller crimper technology for weed control in Mediterranean vegetable organic cropping systems. Eur. J. Agron. 50:11-8.


K Coleman, DS Jenkinson, 1996. RothC-26.3 - a model for the turnover of carbon in soil. In: D.S. Powlson, P. Smith, J.U. Smith (Eds.), Evaluation of soil organic matter models using existing long-term datasets: NATO ASI Series I. Springer-Verlag, Heidelberg, Germany, pp. 237-246.


RT Conant, K Paustian, 2002. Potential soil carbon sequestration in overgrazed grassland ecosystems. Global Biogeochem. Cycles 16:1143.


RT Conant, K Paustian, ET Elliott, 2001. Grassland management and conversion into grassland: effects on soil carbon. Ecol. Appl. 11:343-55.


G Convertini, D Ferri, M Maiorana, L Giglio, P La Cava, 1998. Influenza dell’interramento dei residui colturali sulla sostanza organica e su alcune proprietà biologiche del terreno in una prova a lungo termine in ambiente mediterraneo. Boll. Soc. Ital. Sci. Suolo 47:169-81.


P Falloon, P Smith, 2002. Simulating SOC changes in long-term experiments with RothC and CENTURY: model evaluation for a regional scale application. Soil Use Manag. 18:101-11.


R Farina, K Colemann, AP Whitmore, 2013. Modification of the RothC model for simulations of soil organic C dynamics in dryland regions. Geoderma 200-201:18-30.


RF Follett, JM Kimble, R Lal, 2001. The potential of US grasing lands to sequester carbon and mitigate the greenhouse effect. CRC Press LLC, Boca Raton, FL, USA.


AS Fotheringham, C Brunsdon, M Charlton, 2003. Geographically weighted regression: the analysis of spatially varying relationships. Wiley, New York, NY, USA, pp. 248.


R Francaviglia, A Benedetti, L Doro, S Madrau, L Ledda, 2014. Influence of land use on soil quality and stratification ratios under agro-silvopastoral Mediterranean management systems. Agric. Ecosyst. Environ. 183:86-92.


R Francaviglia, K Coleman, AP Whitmore, L Doro, G Urracci, M Rubino, L Ledda, 2012. Changes in soil organic carbon and climate change - application of the RothC model in agro-silvo-pastoral Mediterranean systems. Agric. Syst. 112:48-54.


AJ Franzluebbers, 2002. Soil organic matter stratification ratio as an indicator of soil quality. Soil Till. Res. 66:95-106.


MM Giuliani, G Gatta, E Nardella, E Tarantino, 2016. Water saving strategies assessment on processing tomato cultivated in Mediterranean region. Ital. J. Agron. 11:69-76.


J González, M Candás, 2004. Materia orgánica de suelos bajo encinas: mineralización de carbono y nitrógeno. Invest. Agrar. Sist. Recur. Fuera Ser. 3:75-83.


L Guo, P Falloon, K Coleman, B Zhou, Y Li, E Lin, F Zhang, 2007. Application of the RothC model to the results of long-term experiments on typical upland soils in northern China. Soil Use Manag. 23:63-70.


ISTAT (Italian Institute of Statistics), 2010. Agricultural census, data referred to the Municipality where the land/livestock are located. Available from: http://dati-censimentoagricoltura.istat.it/ Accessed: 31/01/2016.


DS Jenkinson, 1990. The turnover of organic-carbon and nitrogen in soil. Philos. T. Roy. Soc. B 329:361-8.


DS Jenkinson, HC Harris, J Ryan, AM McNeill, CJ Pilbeam, K Coleman, 1999. Organic matter turnover in a calcareous clay soil from Syria under a two-course cereal rotation. Soil Biol. Biochem. 31:687-93.


DS Jenkinson, JH Rayner, 1977. The turnover of soil organic matter in some of the Rothamsted classical experiments. Soil Sci. 123:298-305.


JMF Johnson, RR Allmaras, DC Reicosky, 2006. Estimating source carbon from crop residues, roots and rhizodeposits using the national grain-yield database. Agron. J. 98:622-36.


H Kirchmann, R Andersson, 2001. The Swedish system for quality assessment of agricultural soils. Environ. Monit. Assess. 72:129-39.


M Kottek, J Grieser, C Beck, B Rudolf, F Rubel, 2006. World Map of the Köppen-Geiger climate classification updated. Meteorol. Zeitschr. 15:259-63.


Y Kuzyakov, G Domanski, 2000. Carbon input by plants into the soil. J. Plant Nutr. Soil Sci. 163:421-31.


PY Le Gal, A Merot, CH Moulin, M Navarret, J Wery, 2010. A modelling frame work to support farmers in designing agricultural production systems. Environ. Model. Software 25:258-68.


RL Lemke, AJ VandenBygaart, CA Campbell, GP Lafond, B Grant, 2010. Crop residue removal and fertilizer N: effects on soil organic carbon in a long-term crop rotation experiment on a Udic Boroll. Agr. Ecosyst. Environ. 105:42-51.


R Leogrande, O Lopedota, F Montemurro, C Vitti, D Ventrella, 2012. Effects of irrigation regime and salinity on soil characteristics and yield of tomato. Ital. J. Agron. 7:e8.


B Ludwig, KL Hu, LA Niu, XJ Liu, 2010. Modelling the dynamics of organic carbon in fertilization and tillage experiments in the North China Plain using the Rothamsted Carbon Model - initialization and calculation of C inputs. Plant Soil. 332:193-206.


P Martiniello, 2011. Cereal-forage rotations effect on biochemical characteristics of topsoil and productivity of the crops in Mediterranean environment. Eur. J. Agron. 35:193-204.


D Nainggolan, J de Vente, C Boix-Fayos, M Termansen, K Hubacek, MS Reed, 2012. Afforestation, agricultural abandonment and intensification: competing trajectories in semi-arid Mediterranean agro-ecosystems. Agric. Ecosys. Environ. 159:90-104.


DM Nash, PM Haygarth, BL Turner, LM Condron, RW McDowell, AE Richardson, M Watkins, MW Heaven, 2014. Using organic phosphorus to sustain pasture productivity: a perspective. Geoderma 221:11-9.


DS Ojima, WJ Parton, DS Schimel, JMO Scurlock, TGF Kittel, 1993. Modeling the effects of climatic and CO2 changes on grassland storage of soil C. Water Air Soil Pollut. 70:643-57.


WJ Parton, DS Schimel, CV Cole, DS Ojima, 1987. Analysis of factors controlling soil organic matter levels in Great Plains grasslands. Soil Sci. Soc. Am. J. 51:1173-9.


M Pisante, 2013. Agricoltura sostenibile. Principi, sistemi e tecnologie applicate all’agricoltura produttiva per la salvaguardia dell’ambiente e la tutela climatica. Il Sole 24 Ore-Edagricole, Bologna, Italy, pp. 340.


Martín JA Rodríguez, J. Álvaro-Fuentes, J Gonzalo, C. Gil, JJ Ramos-Miras, Corb JM Grau, R Boluda, 2016. Assessment of the soil organic carbon stock in Spain. Geoderma 264:117-25.


Sinoga JD Ruiz, S Pariente, AR Diaz, Murillo JF Martinez, 2012. Variability of relation-ships between soil organic carbon and some soil properties in Mediterranean rangelands under different climatic conditions (south of Spain). Catena 94:17-25.


P Serra, X Pons, D Saurí, 2008. Land-cover and land-use change in a Mediterranean landscape: a spatial analysis of driving forces integrating biophysical and human factors. Appl. Geogr. 28:189-209.


JO Skjemstad, LR Spouncer, B Cowie, RS Swift, 2004. Calibration of the Rothamsted organic carbon turnover model (RothC ver. 26.3), using measurable soil organic carbon pools. Austr. J. Soil Res. 42:79-88.


AJ VandenBygaart, XM Yang, BD Kay, JD Aspinall, 2002. Variability in carbon sequestration potential in no-till soil landscapes of southern Ontario. Soil Till. Res. 65:231-41.


WRB (World Reference Base for Soil Resources), 2014. World Reference Base for Soil Resources 2014. International soil classification system for naming soils and creating legends for soil maps. World Soil Resources Reports No. 106. FAO, Rome, Italy.


R Zornoza, RM Rosales, JA Acosta, JM de la Rosa, V Arcenegui, Á Faz, A Pérez-Pastor, 2016. Efficient irrigation management can contribute to reduce soil CO2 emissions in agriculture. Geoderma. 263:70-7.

Figure 1.

Study area (Manfredonia Municipality) located in Apulia Region, Southern Italy. The map of the study area shows the distribution of the 234 land use sites considered for the analysis. Black circles indicate rainfed arable crops succession (ACr); white circles represent irrigated arable crops succession (ACi), and black stars identify pasture systems (grassland; GL).

Figure 2.

Map of initial soil organic carbon content of Manfredonia Municipality.

Figure 3.

Overview of RothC10N model.

Table 1.

Current crop management of winter durum wheat and tomato.

Wheat Tomato
Tillage Plowing Plowing
Sowing/transplanting Mineral N fertilisation 2nd half of November End of April
Pre-sowing/pre-transplanting* 60 kg ha–1 100 kg ha–1
Top-dressed° 60 kg ha–1 100 kg ha–1
Irrigation# Rainfed Automatic
Harvest At maturity At maturity
Crop residue§ Removed Removed

[i] *As diammonium phosphate

[ii] °as ammonium nitrate

[iii] #drip irrigation with water amount refilling 100% of soil water deficit

[iv] §in the current management crop residues were removed up to 85%.

Table 2.

Formulas and values used to calculate plant C input (Mg ha -1).

Wheat Tomato Pasture Fallow
Plant variables
   Yield (Y) 3.53 84.46 - -
   Dry total above-ground biomass 9.23 11.70 6.70 0.50
Source of C*
   C from residues (Cr)=0.1 × (Y/HI) × 0.45 0.38 0.22 0.30 0.23
   C in roots (Crot)=(Y/(HI × S:R) × 0.45 1.25 1.58 0.90 0.07
   C in root exudates (Ce)= 0.09 × (Y/HI)× 0.45 0.38 0.47 0.27 0.02
   C weeds (Cw)=0.07 × (Y/HI) × 0.45 0.29 0.79 0.16 0.01
Total C input (Ct)°
   15% crop residue incorporation 2.29 3.06 1.64 0.33
   100% crop residue incorporation 4.47 4.30 1.64 0.33

[i] Y, yield (Mg ha–1 of dry matter); HI, harvest index; S:R, shoot to root ratio; C, content of plant material set to 0.45.

[ii] *Formulas adapted from Skjemstad et al., (2004), Kong et al. (2005), Kuzyakov and Domanski (2000)

[iii] °Ct is the sum of Cr, Crot, Ce and Cw. In the current management arable crop residues were removed up to 85%. In alternative S1 and S3 scenarios we proposed an incorporation of 100% of crop residues.

Table 3.

Cropping systems, initial and final soil organic carbon stock (Mg ha1) predicted by RothC10N model under different scenarios, in the 234-georeferred crop succession units located in Manfredonia Municipality.

Land use categories Numbers Initial SOC Final SOC (S0) Final SOC (S1) Final SOC (S2) Final SOC (S3)
Arable crops
   Rainfed crop rotation
      DW in continuous 96 44.79±0.60* 45.13±0.44 56.83±0.44 - -
      3-yrs DW-BF 30 45.64±0.99 43.63±0.75 52.02±0.86 - -
   Irrigated crop rotation
      3-yrs DW-T 42 46.03±0.73 41.68±0.48 49.79±0.51 48.45±0.58 58.75±0.57
      5-yrs DW-BF-T 27 45.26±0.77 40.25±0.56 47.01 ±0.61 46.73±0.55 55.57±0.56
   Pasture 39 49.54±0.34 43.74±0.39 51.70±0.44 - -

[i] DW, durum wheat in continuous; BF, bare fallow; T, tomato.

[ii] *Means±standard error.

Table 4.

Cropping systems and 20-yrs cumulated CO2 emissions (Mg CO2 ha1) predicted by RothC10N model under different scenarios, in the 234 georeferenced crop succession units located in Manfredonia Municipality.

Land use categories Numbers S0 S1 S2 S3
Arable crops
   Rainfed crop rotation
      DW in continuous 96 174.60±0.60 306.07±0.62 - -
      DW-DW-BF 30 158.90±2.07 260.61±4.81 - -
   Irrigated crop rotation
      DW-DW-T 42 205.65±1.54 321.43±1.37 180.83 ±0.88 288.58±1.18
      DW-DW-BF-DW-T 27 190.03±1.11 289.13±1.84 166.27±0.86 257.75±2.34
Pasture 39 123.09±4.86 155.46±11.52 - -
Abstract views:


Article Metrics

Metrics Loading ...

Metrics powered by PLOS ALM

Copyright (c) 2016 Claudia Di Bene, Alessandro Marchetti, Rosa Francaviglia, Roberta Farina

Creative Commons License
This work is licensed under a Creative Commons Attribution-NonCommercial 4.0 International License.
© PAGEPress 2008-2018     -     PAGEPress is a registered trademark property of PAGEPress srl, Italy.     -     VAT: IT02125780185