1. Introduction
The forests are a key element in managing the protection and rehabilitation of areas vulnerable to land degradation and erosion. The characteristics of forests and soils are among the main parameters evaluated for natural resource management planning. According toMarion Briens, Dominique Legros and Edouard Michel in the book describing the state of Mediterranean forests in 2013, which the degradation of these lands causes a decrease in agricultural productivity, and compromises essential ecosystem services. At European level, the draft framework directive on soil protection was proposed in 2007. It is based on the observation that 45% of European soils are degraded and poor in organic matter, and stresses. These degradations result in erosion, compaction, loss of organic matter, salinization, landslides, loss of soil biodiversity, acidification. In addition; overgrazing is one of the major causes of soil degradation, with herds too large in relation to the carrying capacity of their routes which, instead of favoring the growth of pasture, often accelerates the desertification process. These problems could be made worse by the effects of climate change. From 1992 to 2009, the areas of arable land decreased by 7 million hectares (-13%) and 4 million hectares (-9%) respectively in the agricultural population of the north and south-east Mediterranean countries. The Mediterranean forest is characterized by a dominant woody stratum with dense undergrowth under development. The types of species encountered and shrubs are: olives (Olea europea ), cork oaks (Quercus ilex ), eucalyptus (Eucalyptus globulus ) and conifers. These latter; are wide, spiny, and possess several important varieties such as: maritime pines (Pinus pinaster ), aleppo pines (Pinus halepensis) and cedars (Cedrus atlantica ). Today, heterogeneous climatic conditions, agro-pastoral practices, and frequent fires (Trabaud, 1979) threaten Mediterranean biodiversity. The real effect of the latter on the forest ecosystem is a current and major problem for the media. Several authors consider that forest fires can prove beneficial to the health of many forest ecosystems. Prescribed burning and deburring are two management and maintenance operations used worldwide. Indeed, insects, fungi and bacteria of all kinds can proliferate in the clumps of foliage and dead branches that cover the ground. Forest fires are a natural way to sterilize the soil, free up space for the growth of new plants and stimulate the growth of herbaceous plants. However, the relationship between soils and forests is much broader and more complex. They also influence the environment as a whole. This interactions help maintain the environmental conditions necessary for agricultural production (Zammit, 2008). Their moderate intensities have an impact on all soil parameters. According to Assunta Pales and al., 2004; the duration of heating, the maximum temperatures, the moisture content, the type of substrates, the quantity and density of the fuel, the severity of the combustion simulate all the reactions of live telluric species alive in the middle. The immediate effect on soil microorganisms is a reduction of their biomass, and in extreme cases; the soil can undergo complete sterilization (De-Banoand and al., 1998). Fire also modifies the specific composition of the microbial community, its reproductive capacity and catalytic performance is distinguished by its temperature sensitivity (Dunn and al., 1985). According to Certini, 2005; the impact of fire on the soil’s biological properties, greatly depends on its humidity levels. The Populations of microorganisms that are physically active in moist soil are more sensitive than dormant populations in dry environment (Dunn and al., 1985). Choromanska and DeLuca (2002) showed that soils of three experienced regions. In Pinus ponderosa andPinus Pseudo-tsugamenziesii ecosystems, their fire-induced microbial biomass decreased at the wettest level and probably due to faster heat transfer than in dry soils. Water allows better leaching than air. Indirectly, we notice on the burned surfaces a modification of the organic matter, which represents the energetic supply, determining the sum of the possible lifespan in the ground. They tend to reduce nutrient levels; however, the concentration and bioavailability of many contents generally increase due to the burning of humus, as well as the mineralization of the constituent elements, which limits subsequent microbial growth. With regard to the fauna of the soil and more particularly the invertebrates. According to Certini, 2005; the direct effects of the fire are less marked than those on the microorganisms, because of the higher mobility which allows a greater potential to escape the heating by deep digging the ground. However, fire reduces litter mass, which significantly reduces the total mass and number of invertebrate species living in the soil. According to Bachelier, 1978; the fire change the microclimate of the soil and by reducing the energy input of plant debris, the bare soil covered with black ash is hotter and drier, with daily increased thermal amplitude. Earthworms, then quiescent in the depth of the soil, are not damaged. On the other hand, micro arthropods suffer a sudden mortality, but easily colonize the medium after a few months. The fire rejuvenates the settlement of arthropods, which, in its absence, evolve towards a more or less different stand, by modifying the environment. According to Vennetier, 2009; in areas usually ravaged by fire, the ecosystem parameters are in equilibrium with their average intensity. Knowing that; stability is maintained around three resources: adaptation of plant species to this diet, ability to rebuild are stocks of organic matter between two fires, viability of soil and humus (fauna, bacteria, fungi). This equilibrium also depends on the physicochemical parameters of the soils modified by fire; they are gradually restored by biological activity. There is therefore a strong interaction between these two phenomena, essential to understand the resistance and resilience of forest ecosystems to fire. The restoration in this depends mainly on the speed of the repopulation of the plant cover. The expected rise in temperatures in the coming years could favor the spread of large forest fires, which would ultimately involve a sharp increase in burned areas (Giec, 2007). According to Ramade (1997), the recurrence of fires has been reduced to 33 years of life expectancy in a Mediterranean reforestation. Quézel and Médail (2003) show that, on average; most Mediterranean sclerophyte plants are covered by fire every 25 years. In this case, the Algerian forests are subject to multiple climatic and anthropogenic attacks (Quézel and Médail, 2003). Kadik, 1987; estimates that he initially covered 7 million hectares; distributed on the northern fringe of the southern foothills of the saharan atlas. This area often represents only 4.1 million hectares dominated by the degraded stratum (DGF, 2000). The deforestation rate is in scale with the climate of northern Algeria; would be reduced from 27.1% to 11% only. The production area is small and represents only 17% of the total forest area; 21% are likely to be improved and 62% are severely degraded (Kadik, 1987). It characterized by a Mediterranean climate with two distinct seasons that of the rains and the drought, and it provokes a fundamental physical character for their forest (Kadik, 1987). The latter is also known for its susceptibility to fires that are very common in the summer and annually destroy over 37000 ha (Benabdeli, 1996). She lost 1162 484 ha between 1979 and 2010 with a total number of 41644 of fires. The broad-leaved species such as oak and beech do not burn as easily as conifers, which are virtually the only component of forests in mountainous regions. Among conifers and pines are more easily burned because of their high resin content. Although conifer needles are extremely flammable, their fields and their branches are significantly less. According to Trabaud, 1992 (a) and (b); the evolution of this forests are constantly conditioned by fires that have a leading role on the dynamics of plant communities in the Mediterranean ecosystem. In this case, the transition of the fire eliminates all vegetation located on the surface and above the soil surface. To know the future of these burned communities, it is essential to follow their evolution over time by carrying out a chronic analysis of which we know the date of the last disturbance. The majority of perennials and plant communities of Mediterranean landscapes are regenerated after fire by vegetative reproduction. Exclusively and rarely case; which species can regenerate by sexual means. In turn, the land clearing is an inevitable destructive action of the vegetation in the place, the final disappearance of the wooded state to another use, widely to respond to needs in the field of agriculture and livestock in the forest. Benabdeli, 1996 and Boudy, 1955; confirm that in the Oranaise region where the reforestation rate does not exceed 9%, the deforestation through land clearing result the intense degradation of chains coastal forests, in addition mainly sheep and goat are often considered primarily responsible for the degradation of plant ecosystems (Alexandrian and Esnault, 1998). According to Benabdeli (1996), the grazing in the forests is a very degrading factor by its aggressiveness and the damage it causes to the vegetation and soil. It is a source of partial or total removal of the vegetation cover. The grazing in forest unregulated imposes significant damage: livestock cut young terminal shoots of trees for food, jeopardizing their growth and sometimes their existence (Seïgue, 1985). This operation facilitates the grazing of the stratum bushy palatable and pruning of shrubs (Benabdeli, 1996). Herds eat forest grains including acorns there by reducing opportunities for regeneration thus compromising its durability. The grazing in forests facilitates the development of carpet herbaceous and can be for farmers an incentive to cause fires (Seïgue, 1985). This contribution aims to study the spatiotemporal evolution of the forest and soil of the municipality of Tenira located in western Algeria. The latter has undergone deep ecological and floristic changes. According to statistics of DGF (2013), each year Tenira forest is burned; whose thousand hectares have been lost. For this purpose; this analysis focuses on the description of the general state of the Tenira forest and soils from 1987 to 2018 using spatial tools of multi-spectral data and medium resolution. The integration of the use of remote sensing linked to forest fires is a real opportunity to bring together the national and international community. The different aspects of management and research will be addressed including, among others, the areas related to fire monitoring and post-fire mapping. In addition to covering a variety of land-to-space uses, this research article also addresses current issues such as drone use, international collaboration, and forest fire costs. Among the main objectives of this contribution is to encourage the community to present the state of frequent capabilities in the field of remote sensing applied to the different phases of forest fire management and research (fire, during fire and after-fire). To understand better the challenges associated with the exploitation of remote sensing and the integration of research results into operational fire management activities. To identify also areas of collaboration to link soil, air and space with the goal of strengthening forest fire management in our country and elsewhere. Bringing together leaders and experts from the remote sensing and fire community to explore, interpret, establish and strengthen collaboration and partnerships in the areas of forest fire research and management.