At the conference of the Italian Association of Agricultural Scientific Societies (Associazione Italiana Società Scientifiche Agrarie, AISSA) held in Palermo, Sicily (28th-29th November 2012), a presentation was given on Soil degradation processes in the Italian agricultural and forest ecosystems on behalf of the Italian Soil Science Society (SISS) and the Italian Society of Pedology (SIPe). This paper is the follow up of that report and presents the state of the art of soil degradation in Italy from a scientific standpoint. The aim of this short review is to illustrate the nature, economic relevance, and territorial impact of soil degradation in the Italian agricultural and forest ecosystems and in a European context. It also highlights the most important research needs and perspectives of soil conservation.
Soil functions and soil degradation processes
Soil is a multi-phase and complex natural system, which tends to self-organize according to the factors of pedogenesis (Figure 1). Figure 1 shows a soil profile in the Veneto Po Plain, on a terrace formed by the river Adige. Under the first 30 cm of the plough layer, where macroporosity is enhanced by cultivation and accumulation of organic matter, there is a structured and slightly rubified horizon that gradually passes to the fine sandy fluvial parent material at a depth of approximately 70 cm. The groundwater fluctuates around approximately one meter from the surface. The millennial physical, biological, and chemical transformation of the unweathered sand into soil has allowed the development of its major functions, i.e. the biomass production for agricultural uses and the filtering of pollutants, which protects groundwater from contamination. The self-organization process is finite in time and tends to reach a steady state in which entropy is minimized (Addiscott, 2010; Targulian and Krasilnikov, 2007). Soil self-organization can be observed on different levels (Phillips et al., 1999; Phillips, 1995) and in the context of field survey, it can be understood by the arrangement of its constituents in specific and distinctive forms, namely soil horizons and pedofeatures. From an eco-systemic standpoint, soil self-organization is part of a country’s natural heritage, but it also has economic value because the interests of soil self-organization and ecosystem services run parallel (Robinson et al., 2009). Therefore, soil degradation can be defined as the process leading to the loss of the self-organization ability of the soil constituents, due to either natural causes or human activities.
Another definition of soil degradation, more specifically directed towards emphasizing the loss of soil functions, is that given by the Organisation for Economic Co-operation and Development (OECD) which states that soil degradation refers to the process(es) by which soil declines in quality and is thus made less fit for a specific purpose, such as crop production (OECD, 2001).
In reality, soil functions are multi-fold, and many of them have still not been completely investigated. The European Union summarizes soil functions in seven categories (European Commission, 2006a; JRC, 2011): i) Biomass production, including that in agriculture and forestry; ii) Storing, filtering and transforming nutrients, substances and water; iii) Biodiversity pool, such as habitats, species and genes; iv) Physical and cultural environment for humans and human activities; v) Source of raw materials; vi) Acting as a carbon pool; vii) Archive of geological and archaeological heritage.
Several factors could impair soil function. The European Union has acknowledged eight threats to soil functions, or degradation processes: i) Water and wind erosion; ii) Decline in organic matter; iii) Contamination; iv) Sealing; v) Compaction; vi) Soil biodiversity loss; vii) Salinization; viii) Floods and landslides (European Commission, 2006a).
The OECD also considers submersion, surface crusts and compact layer formation along the profile, deterioration of the soil structure, accumulation of toxic substances, as well as loss of nutrients (OECD, 2001). Other soil degradation processes have been indicated by several authors, in particular, soil losses for suffusion in karst and granite (Li and Zhou, 1999; Durgin, 1984), modification in cracking of Vertisols due to climate change (Pal et al., 2009), increased soil aridity as a consequence of reduced water holding capacity and climate change (Costantini et al., 2009; EEA, 2012), colder soil temperature regime because of the reduction in snow cover (Freppaz et al., 2008), loss of pedodiversity as a consequence of human activities (Dazzi and Lo Papa, 2013; Dazzi and Monteleone 2007; Costantini and L’Abate, 2009), peat degradation and loss of hydric properties following drainage (Fornasiero et al., 2003).
Relevance of soil degradation
Some attempts have been made to estimate the costs of soil degradation. In the accompanying document to the thematic strategy for soil protection (European Commission, 2006b), the impact assessment of only the direct annual costs of the main soil degradation processes in Europe is estimated to amount to over 38,000,000,000 euro per year. In Italy, the direct costs of the hydrogeological instability experienced during the last ten years, caused by landslides, floods, and soil erosion, is estimated to be as high as 9,000,000,000 euro (ISPRA, 2013). It goes without saying that hydrogeological instability has a huge impact on human safety. For example, only in the period 2004-2010 there were 67 casualties in 14 landslides (http://www.meteoportaleitalia.it/).
Besides danger to the population and damage caused to buildings and infrastructures, soil degradation has a big affect on the agricultural and forestry sector. In this case, the costs of soil degradation can also be estimated in terms of loss of potential agricultural production capability. The term land take refers to the area of land that is taken by the infrastructure itself and by other facilities that necessarily go along with the infrastructure, such as filling stations on roads and railways stations (http://glossary.eea.europa.eu). On a European level, the loss of winter wheat yield caused by land take during the years 1990 to 2006 has been evaluated at over 6 million tonnes (JRC, 2011). For Italy, the potential loss is assessed to be as much as 474,400 tonnes per year.
The loss of ability to produce food commodities is particularly relevant for Italy as a country, especially if we consider that: i) the price index of cereals has increased considerably during the last ten years (>70%) (FAO, 2013); ii) crop yields per hectare (ha) of main crops have almost reached a plateau; iii) Italy’s self-sufficiency in food has decreased from more than 90% in the 1990s to less than 80% since 2010 (MiPAAF, 2012).
A major consequence of soil degradation in Italy is that it reduces the agricultural production potential of soils that are in many cases already disadvantaged with respect to European standards. It is well known that agricultural areas in Italy are mainly concentrated on the plains and low hilly lands (Figure 2). A recent study actually demonstrates that, according to the European legislation (REG. CE n. 1698/2005), approximately 82% of the total 12.9 million ha of land used for agricultural purposes in the year 2011 must be considered less favored (MiPAAF, 2013). It is interesting to note that among the bio-physical criteria used to single out municipalities with predominantly less favored agricultural lands, soil constraints (limited soil drainage, unfavorable texture and stoniness, shallow rooting depth, poor chemical properties) actually play the most important role (Figure 3).
Impact of soil degradation in Italy and Europe
The European Commission has recognized soil sealing, soil erosion, and organic matter decline as the soil degradation processes on which member states should concentrate their main efforts, in consideration of their economic and environmental relevance (Resource Efficiency Roadmap: COM no. 571 of 20/9/2011). In this respect, the following objectives for the year 2020 have been recommended: i) reducing annual land take, i.e. the increase of artificial land should not exceed 800 km2 per year in the EU; ii) there should be an at least 25% reduction in areas of land in the EU that are subject to a soil erosion rate of more than 10 tonnes per ha per year; iii) there should be no overall decrease in soil organic matter levels and no increase in soils currently with less than 3.5% organic matter.
Soil sealing and land take
Soil sealing is the most harmful process of soil degradation, since it often implies the complete loss of biological functions, it is almost irreversible, and threatens a vast amount of soils, in particular, those most fertile. The area of the soil surface covered with an impermeable material is today estimated to be approximately 9% of the total European Union. During the years 1990-2000, the sealed area in the then 15 EU member states increased by 6%; at present, the demand for both transport infrastructures and new buildings continues to rise (JRC, 2011).
The territory directly covered by settlements in Italy increased by 166% between 1956 and 2012, at a daily rate of approximately 100 ha (Consiglio dei Ministri, 2012) and currently involves 4.9% of the country (ISPRA, 2013). This does not include the network of roads (approx. 1000 km) and railways (approx. 16,000 km).
Per capita soil consumption doubled from 2.8% in 1956 (170 m2 per capita) to 5.7% in 1996 (303 m2 per capita), and reached 6.9% in 2010 (343 m2 per capita) (ISPRA, 2013). Since the beginning of the 1980s, the increase in sealed areas was decoupled from population growth, indicating that land take and urban development have generally occurred through dispersed residential settlements, as well as commercial and infrastructure expansion (Munafò et al., 2013). The highest proportion of sealed plots has been observed in northern Italy. In contrast, the per capita growth rate of land take is higher in southern Italy.
A more recent threat jeopardizing agricultural soils in Italy is the installations of photovoltaic devices to produce electricity that occupy agricultural land of different dimensions. They are mostly located on flat areas or valley floors that have high productive value. It is still not understood how photovoltaic devices modify or impair soil function. However, the land used for this purpose is certainly no longer agriculturally productive.
Although no estimates are available as to the number of hectares covered or the kind of soils involved, the total number of installations gives an indication of how widespread their use is. At the end of 2009, there were 71,284 photovoltaic installations in Italy for a productive capacity of 1142.4 MW (Dazzi and Lo Papa, 2013). At present, only some regional administrations have started to consider the problem of legislation, e.g. Tuscany (http://www.arpat.toscana.it/documentazione/normativa/normativa-regionale-toscana/2013/delibera-consiglio-regionale-toscana-n.15-2013).
In conclusion, unless new national legislation is introduced, Italy, like the rest of Europe, is most probably destined to fail to achieve the European objective to reduce the rate of annual land take by 2020.
Soil erosion and landslides
The European Environment Agency (EEA) estimates that 115 million ha, or 12% of Europe’s total land area, are affected by water erosion, and that 42 million ha are affected by wind erosion (JRC, 2011). The OECD estimates that over 20% of Italian agricultural land fell within the moderate to severe risk classes for soil water erosion (equal or more than 11 t.ha–1.y–1) in the period 2000-2002. The Institute for Environmental Protection and Research has mapped some 485,000 landslides in Italy, taking up 2,070,000 ha, i.e. 6.9% of the country, and has mapped the areas of row crops (Figure 4) and woodland (Figure 5) at different degrees of criticality (ISPRA, 2013).
Critical areas at risk of soil erosion are located in central and southern Italy, on slopes where agricultural lands are intensively cultivated and there are outcrops of marine sediments of the Neocene. In contrast, woodlands with the highest risk of landslides are more widespread in northern Italy, on the steep slopes of the Alps and the Apennines.
It must be stressed that most shallow landslides concern the soil cover, not the substratum, and they are caused by a complex interaction between climate, morphology, soil characteristics, forest land use, and management. Therefore, only taking into consideration the nature of the soil it is possible to understand the causes and to identify the technical measures to be taken to prevent this kind of mass movement. For example, it has been well documented that the improper management of woodland on Andosols placed on fragile morphologies can dramatically increase the risk of landslides (Iamarino and Terribile, 2008; Terribile et al., 2007) (Figure 6).
Under the current legislation and land management policies, Italy will probably not achieve the 2020 European target for soil erosion rates. Fluctuations are expected and these reflect the patterns of land use and climate change. However, the lack of robust and validated models, which include the effect of land management, means that reliable quantitative projections are currently not available, neither for Italy nor for Europe as a whole (EEA, 2012).
Different forms of soil degradation often occur at the same place and time as a consequence of a triggering event. In Figure 7 we can see how excessive land leveling deeply scalped the soil, not only provoking the loss of material and increasing the risk of floods and landslides, but also worsening soil organic matter content and biodiversity, which in turn loosened soil structure and favored surface crust formation.
Organic matter decline
It has been estimated that 45% of European soils have a low or very low organic carbon content (0-2 g.100 g–1) and 45% have a medium content (2-6 g.100g–1) (JRC, 2011). Data downscaled to Italy indicated that almost 23% of Italian soils have less than 1 g.100 g–1 of organic carbon [i.e. 1.72 g.100 g–1 soil organic matter content (SOMC)] concentrated in the regions of Apulia, Sicily and Sardinia (Jones et al., 2005; Panagos et al., 2008; Schils et al., 2008).
The results reported by many authors suggest that changes in land use and management might be responsible for the variations in SOMC in the country as a whole and on a regional level (Smith et al., 2012). The information stored in the national soil information system of Italy database confirms the influence of land use and management on SOMC in this country (Table 1). Data on SOMC in the surface horizons are stored for 23,516 sites. There is a remarkable range in SOMC mean values between different crops and uncultivated land. In particular, rice paddies and other arable lands (urban soils included) show mean values of between 2.0% and 2.3%, mean SOMC values for meadows and other less intensively or uncultivated areas vary between 3.0% and 3.9%, whereas in the different kind of woodlands and natural areas these values can reach 6.0%. However, the high values of standard deviation, which are of the same order of magnitude as means, or even higher, indicate that variations of land management and local conditions play an important role in regulating SOMC.
Therefore, we can expect to see important changes in SOMC over time. On a national basis, Fantappiè et al. (2010) estimated, by means of a multivariate spatial regression model, a significant decrease in SOMC (from 2.53 to 2.02 g.100g–1) between the 30-year period 1961 and 1990, and the period 1991 and 2009. Meadows (from 2.69 to 1.93 g.100g–1) were more affected than forests (from 3.34 to 2.77 g.100g–1) and arable lands (from 1.55 to 1.36 g.100 g–1). The decrease was most likely due to the changes in land use and management, while the observed climate change occurred between the two periods was not seen to play a key role. Nevertheless, climate may have had an influence in meadows and in arable lands with a moderate or high mean annual precipitation decrease (<–100 mm.y-1) and a moderate to high increase in mean annual temperature (>0.62°C), largely distributed in Apulia, Sardinia, the northern Apennines, and the pre-Alps (Fantappiè et al., 2011).
Critical levels of SOMC are still a question of debate and are thought to differ according to the kind of soil function (e.g. plant mineral nutrition, soil physical properties), particle size, and climatic region (Loveland and Webb, 2003). Some authors considered the threshold of 1.72 g.100 g–1 as the minimum value to assure the supply of elements to plants and to limit the passage of pollutants from the soil surface to the underlying water table (Johnston, 1991; Körschens et al., 1998; Huber et al., 2008; APAT, 2007). The SOMC for approximately 34% of the Italian topsoils studied falls below that limit, and 80% falls below the target threshold of 3.5 g.100 g–1 (i.e. the established target in the above mentioned EU Resource Efficiency Roadmap). Therefore, it is possible to conclude that approximately one-third of a representative set of Italian soils can be considered to be degraded in some degree for a number of their basic functions.
Degraded soils are mainly under agricultural cultivation, but they are also present in a significant proportion of the semi-natural land covers. Complying with the objectives stated in the Resource Efficiency Roadmap for the year 2020, and restoring the fertility of Italian soils, would require a major effort to launch a nation wide campaign dedicated to the implementation of specific, locally tailored agro-techniques across all agricultural land uses.
Among soil management practices, irrigation is thought to have a considerable effect on the physical and chemical properties of the soil. The impact of irrigation on soil organic matter sequestration, however, is controversial, depending on the interaction with many other agricultural practices, such as type of cultivation, fertilization, volumes and time of irrigation. Some authors claim that, in the Mediterranean environment, irrigation causes a decrease in SOMC of arable lands because it enhances microbiological activity and mineralization (Alvaro-Fuentes and Paustian, 2011). However, others, on a broader scale, report the opposite (Chen et al., 2011).
The data stored on the national soil database, limited to the regions of central and southern Italy, indicate lower SOMC values for all crops under irrigation, particularly for vegetables, row crops, and orchards (Table 2). Vineyards, olive tree groves, and mixed crops show fewer differences, and the same holds true for meadows. Irrigation of tree crops is sometimes combined with a permanent grass cover that avoids soil surface cultivation during the crop season. It is well known that this practice, aimed at eliminating weeds and reducing capillary water losses in rain-fed cultivation, usually leads to a decrease in SOMC (Conant et al., 2001).
After soil sealing, erosion, and organic matter decline, compaction is probably the most extensive degradation process affecting soil resources of Europe and Italy. Compaction is strictly bound to soil structure deterioration that is often induced by the use of heavy machinery on soils with a low organic matter content. Therefore, progressive soil compaction frequently goes along with organic matter decline.
Compacted soils, showing bulk density (BD) values over 1.4 g.cm3 generally have bad structure conditions, few macropores, show impediments to regular air and water flows, and limit microbiological activities (Pagliai et al., 2000).
Estimates of areas at risk of soil compaction vary according to the authors. A recent approximation classifies around 36% of European soils as having high or very high susceptibility to compaction, while other sources report 32% of soils being highly vulnerable and 18% moderately affected (JRC, 2011).
Italian soils are considered to be affected to a similar extent (APAT, 2007). The national soil database indicates that 2186 out of 8125 sites where BD was measured are compacted (27%). They are present in all the cultivated hill lands and on the plains of Italy, particularly when soil texture is fine and organic carbon is low. Table 3 shows a strong relationship between land use and soil compaction. In fact, rice paddies, wetlands, degraded natural areas, and rain-fed row crops are those contexts in which soils more frequently have BD values over 1.4 g.cm3. Mountain meadows and woodlands, but also irrigated row crops, have the most friable and porous soils (Figure 8).
Salinization, sodification, and alkalinization
Salinization is the accumulation of soluble salts (mainly chloride, sulphate, carbonate and bicarbonate of sodium, magnesium, calcium, and potassium) in the soil profile. Sodification is the progressive saturation of the exchange complex with sodium (mainly from sodium carbonate), while alkalinisation is the increase in pH reaction in the soil solution up to or over 8.5.
Soil salinization in Europe is estimated to affect between 1 to 3 million ha, mainly in the countries of the Mediterranean (JRC, 2011). The phenomena is thought to be increasing as a consequence of the rise in evapotranspiration demand caused by the ongoing climate change and, to a greater extent, by the harsher competition seen every day between the different needs for water. In fact, this latter factor means that the water used for irrigation is of an increasingly poor quality.
In Italy, salinity and sodicity are commonly believed to have only a marginal effect (Tóth et al., 2008) and to be concentrated along some coastlines and in Sicily (Dazzi, 2006). However, studies on gypsiferous soils and on soils with parent materials rich in sodium (Dazzi et al., 2005; Busoni et al., 1995) have demonstrated that the presence of soils with a Saline or Sodic horizon might be more extensive than currently estimated, and, in particular, much larger than that of Solonchak and Solonetz.
In addition to the scientific results, regional soil surveys have reported the presence of saline and sodic soils in different parts of the central and southern regions, and also in northern Italy (Figure 9). The world reference base for soil resources soil classification system currently considers many kinds of salt-affected soils, besides Solonchaks, Solonetz, and Gypsisols. In particular, the sodic qualifier applies to soils that have 15% or more exchangeable sodium (Na) plus magnesium on the exchange complex within 50 cm of the soil surface throughout. The Hyposodic qualifier considers eligible soils that have 6% or more exchangeable Na on the exchange complex in a layer, 20 cm or more thick, within 100 cm of the soil surface. Salic soils must have a salic horizon starting within 100 cm of the soil surface and hyposalic soils an ECe of 4 dS m–1 or more at 25°C in some layer within 100 cm of the soil surface. A salic horizon must have: i) averaged over its depth at some time of the year, an electrical conductivity of the saturation extract (ECe) of 15 dS m–1 or more at 25°C, or an ECe of 8 dS m–1 or more at 25°C if the pH (H2O) of the saturation extract is 8.5 or more; and ii) averaged over its depth at some time of the year, a product of thickness (in centimetres) and ECe (in dS m–1) of 450 or more; and iii) a thickness of 15 cm or more. Several hundred profiles stored in the national soil database have at least one of the sodic, hyposodic, salic, hyposalic, and gypsic qualifiers; they belong to Vertisols, Cambisols, Regosols, Calcisols, and in a few cases to other soil classes. The distribution area of all kinds of salt-affected soils is 31,968 km2 (Figure 10). The presence of salt-affected soils is not only limited to the south of Italy or coastal areas, but to the north as well. However, the occurrence of soils influenced by salinity or sodicity in the topsoil is much less widespread than that of soils that are only affected at depth.
It has been reported that irrigation with bad quality water in Italy is on the increase and can raise soil salinity (Crescimanno et al., 2009). A data search through the national soil database for the electrical conductivity of irrigated and non-irrigated soils of southern Italy gave the results reported in Table 4. The soil electrical conductivity was compared between 321 irrigated and 716 non-irrigated sites. All sites refer to the regions of southern Italy, where problems related to the use of bad quality water are more critical because of the limited supply of fresh river and lake water, and the high proportion of wells placed close to the Mediterranean coast. Nevertheless, average values of electrical conductivity point to low saline conditions. In particular, the outcomes show that a significant increase in salinity of irrigated soils is only present in vegetables and meadows, while in the other crops, irrigation either did not affect soil salinity significantly or contributed to salt leaching.
Saline and sodic soil distribution in Italy also depends on other agricultural practices, such as land leveling before crop plantation on soils formed from marine substrata (Figure 11). The extent of this kind of degraded soils is still not completely understood.
Driving forces of soil degradation
Unfavorable climate quality and climate changes, unsustainable intensification of agricultural activities, and pattern of population growth are the processes considered to play the most important role in determining vulnerability to soil and land degradation in Italy (Salvati et al., 2011). According to four different scenarios, in the year 2015 up to 18-27% of the country will be affected in various degrees by land degradation (Salvati and Carlucci, 2013).
More sensitive terrain is mainly located in coastal and upland areas of southern Italy and the main islands and, to a lesser extent, in some plains of northern Italy where population density is higher (Costantini et al., 2009; Salvati et al., 2011). However, recent studies seem to indicate a tendency to dissociate population density and land degradation. As a matter of fact, since the 1980s, the population has increased in moderately vulnerable areas but has decreased where there is highly vulnerable land (Salvati, 2012).
Several studies have demonstrated that land policy, determined by EU regulation and its practical application by local authorities and farmers, can either enhance or impair land use sustainability and soil conditions. Management practices introduced with the cross compliance Good Agricultural and Environmental Conditions (GAEC) standards were found to be effective in improving soil qualities (Bazzoffi et al., 2011), in particular, those that minimized soil disturbance and increased soil organic carbon (Basso et al., 2012).
On the other hand, soil erosion in some parts of southern Italy has been shown to be associated with specific types of changes in land use as well being promoted by agricultural policy. The application of the F measure of Reg. CE 2078/92, for instance, which implies a 20-year period of set-aside for remodeled areas, is thought to cause an increase in soil erosion and degradation in southern Italy (Piccarreta et al., 2006).
Conclusions and research needs
Soil degradation processes in Italy not only have specificities with respect to northern European countries, but also to the other Mediterranean nations. In fact, if the impact of soil sealing, organic matter decline, and soil compaction are on average comparable to many other countries, landslides (involving/evolving on soils), soil erosion, and soil salinization often cause more damage in Italy than in most other parts of Europe. On the other hand, the fight against soil degradation is certainly more difficult in Italy than in other European countries because of the high environmental variability that means that application of soil and water conservation systems has to be finely tuned (Corti et al., 2013).
The most important driving forces of soil degradation are unfavorable soil and climate conditions coupled with poor environmental management, improper land planning, and bad agricultural husbandry. Among the different drivers, careless soil and land management of fragile environments (the responsibility of both public administrators and farmers) is the most important cause of soil degradation (Terribile et al., 2013).
Driving forces of soil degradations act on different levels: national, regional, municipal council and the farm. Therefore, the only response to combat land degradation is represented by integrated policy measures carried out on different spatial levels (Salvati et al., 2011).
The soil degradation process that causes the most damage in Italy is certainly the irreversible loss of land caused by urbanization and other non-agricultural uses, which often affects the most fertile soils of the plains. At present, among the different services that are lost with soil sealing, the diminished capability to produce food is particularly relevant, as it increases the gap between the Italian primary sector with the other developed countries in terms of food self-sufficiency. Soil sealing is particularly widespread in all flat areas, exactly where landslides and floods cause more damage.
Soil erosion and mass movements are still the most widespread forms of soil degradation in many regions of Italy. Landslides and floods, soil organic matter decline, and loss of biodiversity are all linked to water erosion. Besides reducing soil fertility, water erosion impairs several other eco-services, e.g. quality of foods and landscape, and biodiversity.
Further less devastating and less visible but still widespread processes are threatening Italian soils. Among them, soil compaction is assuming an important role as a consequence of the increasing use of heavy machinery for many agricultural practices in soils with a poor organic matter content. The risk of soil salinization and sodification is also destined to increase as a consequence not only of intensified competition among different water uses, but also because of the diffusion of excessive land leveling in soils formed from marine sediments.
Many other still less visible and less known soil degradation processes affect the soil resources of Italy, among them, the loss of the cultural value of soil, which is often accompanied by the decrease in pedodiversity, and the loss of the traditional landscapes (Dazzi and Lo Papa, 2013). The process is mainly caused by crop intensification, practised on unsuitable soils or with improper agro-techniques, and is linked to the increase in hydrological disorder and geomorphological risk. But the relevance of this process is also to be found in the consequences of damage to the natural beauty of the landscape, as well as in the worsening of soil suitability for quality crops (Costantini and Barbetti, 2008). The degradation process is often underestimated, since Italy is still one of richest places in the world in terms of soil and landscape diversity, but the rapid disappearance of the cultural value of soil means our landscapes are becoming less and less attractive every day.
The picture outlined in this short review helps highlight some of the research needs to which soil sciences can be directed, in collaboration with the other agricultural sciences. First of all, there is the need to improve our basic knowledge. Our understanding about many soil degradation processes in Italy is still incomplete, both because some processes have still not been much investigated, and since the great Italian pedodiversity has not yet been completely surveyed and made available through online databases.
Reliable, sensitive, and locally validated models are still not available, especially for complex degradation processes such as soil water and mass erosion (Dazzi and Lo Papa, 2013). Monitoring soil characteristics and qualities must rely upon direct assessment or intensive validation, possibly by means of proximal and remote sensors (see, for example, http://www.isoil.info/). We also do not know much about the resilience of different soils against degradation processes and their reaction to the measures foreseen under the current European agricultural policy (Bazzoffi and Zaccarini Bonelli, 2011). Finally, cooperation between policy makers and stakeholders is still in its infancy, and even more so with regards to the integration of soil and agronomic sciences with the social and economic disciplines. These factors often limit the impact and effectiveness of scientific research and results on land planning and management.
|Land use||Mean||Standard deviation||Sites (n)||SOMC<1.72 (% of sites)||SOMC<3.5 (% of sites)|
|Olive tree groves||2.29||1.87||1816||41||85|
|All land uses||2.95||3.41||23,516||34||80|
SOMC, soil organic matter content (g.100 g–1).
|Land use||SOMC||Standard error||Sites (n)|
|Vegetables not irrigated||2.38||±0.28||80|
|Row crops irrigated||1.96||±0.04||1517|
|Row crops not irrigated||2.06||±0.03||2288|
|Orchards not irrigated||2.80||±0.13||289|
|Vineyards not irrigated||2.06||±0.09||438|
|Olive tree groves irrigated||2.00||±0.07||472|
|Olive tree groves not irrigated||2.08||±0.05||855|
|Agricultural mixed irrigated||1.67||±0.16||37|
|Agricultural mixed not irrigated||2.04||±0.11||153|
|Meadows not irrigated||2.48||±0.17||392|
|All land uses irrigated||2.03||±0.11||3040|
|All land uses not irrigated||2.27||±0.12||4495|
SOMC, soil organic matter content (g.100 g–1).
|Land use||Mean||Standard error||Sites (n)||BD>1.4%|
|Rain-fed row crops||1.29||±0.00||3984||33|
|Degraded natural areas||1.28||±0.14||5||40|
|Olive tree groves||1.21||±0.01||722||23|
|Irrigated row crops||1.16||±0.01||470||12|
|All land uses||1.24||±0.003||8125||27|
BD, bulk density (g.cm–3).
|Land use||Electrical conductivity||Standard error||Sites (n)|
|Vegetables not irrigated||0.33||±0.05||35|
|Meadows not irrigated||0.32||±0.05||73|
|Row crops irrigated||0.32||±0.03||119|
|Row crops not irrigated||0.48||±0.05||310|
|Orchards not irrigated||0.58||±0.17||57|
|Vineyards not irrigated||0.38||±0.07||119|
|Olive tree groves irrigated||0.23||±0.03||63|
|Olive tree groves not irrigated||0.32||±0.05||106|
|Agricultural mixed areas irrigated||0.20||±0.01||2|
|Agricultural mixed areas not irrigated||0.27||±0.05||16|
|All land uses irrigated||0.34||±0.08||321|
|All land uses not irrigated||0.38||±0.7||716|