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.