Forest Fragmentation Dynamics in the Direct Influence Area of Iguaçu National Park, Brazil

doi:10.21203/rs.3.rs-4669654/v1

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Forest Fragmentation Dynamics in the Direct Influence Area of Iguaçu National Park, Brazil

https://doi.org/10.21203/rs.3.rs-4669654/v1

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The landscape in the Gonçalves Dias river sub-basin is composed of the eastern portion of Iguaçu National Park and the agricultural matrix, inserted within its direct influence area. The sub-basin covers a priority area for biodiversity conservation and restoration in Paraná, as well as encompassing a strategic area for the formation of ecological corridors. We assessed the temporal dynamics of forest fragments in the eastern direct influence area of Iguaçu National Park and identified the predominant factors for the current landscape configuration. We used Geoprocessing techniques for the automatic delimitation of the sub-basin and Remote Sensing for the spatiotemporal analysis of Landsat images at 15-year intervals (1986, 2001, and 2016) to determine the history of land use and land cover changes. We obtained metrics and indices of the fragments composing the landscape of the agricultural matrix in 2016. Our spatiotemporal analysis revealed that the agricultural matrix was already fragmented in 1986 and that there was an increase in native forest cover during the analyzed period. We identified physical constraints for the implementation of agricultural activities, which were related to the native forest cover rate and its distribution. Of the 204 forest fragments identified in the landscape, 90% have an area below 50 ha. The fragmented landscape in the direct influence area of Iguaçu National Park was the result of the historical process of predominantly agricultural land use, guided by the few physical constraints of the relief.

Subtropical forest

Atlantic Forest

Paraná

Remote Sensing

The Atlantic Forest encompasses a vast heterogeneous region in Brazil, including a wide variety of forest physiognomies and floristic compositions, distributed across diverse topographic and climatic conditions (Metzger, 2009). However, data from the SOS Mata Atlântica Foundation and the National Institute for Space Research (Atlântica, 2016) indicate that only 12.5% of the original Atlantic Forest coverage remains in Brazil, spread across 17 states.

Contributing to this percentage is Iguaçu National Park (INP), a strict conservation unit that protects the largest remnant of the Atlantic Forest in Paraná (Tambosi et al., 2014). With an area of 185,262.50 ha (IBAMA, 1999), INP harbors remnants of the Seasonal Semideciduous Forest (SSF), Mixed Ombrophilous Forest (MOF), and the ecological tension area of these vegetation types (IBGE, 2012).

However, despite being protected, conservation units still suffer influence from disturbances originating in matrices with higher agricultural suitability (Sodhi et al., 2010), which worsen according to the longevity of the human occupation history (Tambosi et al., 2014) and further contribute to the scarcity of natural remnants, accentuating the fragmentation process. In this context, the priority is renewed in maintaining remnants located in agricultural matrices, both for the conservation of the remaining biodiversity and for providing reference information for the ecological restoration of degraded areas in the landscape (Daronco et al., 2013).

Landscape Ecology employs models for describing and analyzing landscape dynamics, seeking relationships between spatial patterns and ecological processes. In these analyses, Remote Sensing science is employed, using images from orbital remote sensors as a tool for monitoring vegetation types in the landscape, in order to determine their frequency, distribution, and the connectivity necessary for the maintenance and dispersal of target species.

Methodologies for orbital image analysis may include multispectral analysis (investigating the spectral characteristics of pixels) or spatiotemporal analysis, which involves identifying probable changes in the spectral characteristics of pixels composing the surface over a certain period (Delgado et al., 2012).

The regularity, temporality, and availability of orbital images have been utilized by various authors in landscape analyses (Joly et al., 2014), with the possibility of adopting these techniques in studies with diverse spatial scales. They are applied in the development of conservation proposals at the ecoregional level, in the analysis of landscape within a watershed, in the study of geomorphological compartments (Pereira et al., 2013), in geographical microregions (Olegário et al., 2014), in the direct influence area of conservation units (Grise & Biondi, 2012), in the proposal of regional ecological corridors (Muchailh et al., 2010), and even at a local scale for characterizing land use on rural properties (Gomide & Lingnau, 2009) and analyzing connectivity with neighboring properties (Vidolin et al., 2011).

The study area is considered a priority for biodiversity conservation and restoration in Paraná (IPARDES, 2010b) due to its advanced fragmentation, ecological importance, and strategic location in the regional and national context as the largest conservation unit of the Interior Atlantic Forest. It is also a strategic area in proposals for biodiversity corridors between other Brazilian states and Argentina (Di Bitetti et al., 2003). Therefore, we assessed the temporal dynamics of forest fragments in the eastern direct influence area of Iguaçu National Park and identified the predominant factors for the current landscape configuration.

Study Area

The Gonçalves Dias River sub-basin belongs to the Iguaçu river basin, inserted within the Hydrographic Unit for Water Resources Management (UHGRH) of the Lower Iguaçu. Located between the geographical coordinates 25°02' 40.49" South, 53° 45' 51.89" West and 25° 29' 46.70" South, 53° 34' 08.64" West, the sub-basin has a total area of 49,522 ha, partially covering the municipalities of Santa Tereza do Oeste, Lindoeste, Santa Lúcia, Capitão Leônidas Marques, and Céu Azul, in the western Mesoregion of Paraná, Brazil (IPARDES, 2010a).

It is situated in the Third Paraná Plateau, within the morphocultural subunit of the Lower Iguaçu Plateau, where the terrain consists of elongated and crested hilltops, with straight slopes and V-shaped valleys, at altitudes ranging from 220 to 800 meters (Santos et al., 2006). The predominant soils are Haplic Gleysols, Litholic Neosols, Latosols, and Red Nitosols, all with clayey texture (ITCG, 2016).

The climate is classified as Cfa, humid subtropical with hot summers (Aparecido et al., 2016), and the average annual precipitation recorded for the period from 1986 to 2015 was 1,924 mm, with a daily average of 110.6 mm. The Gonçalves Dias river divides the sub-basin into two distinct realities. On the left bank lies the eastern portion of Iguaçu National Park (INP), while on the right bank (western portion), agricultural land predominates (Fig. 1). As it encompasses the direct influence area of a conservation unit (BRASIL, 2000), the management plan guides the adoption of conservation practices on rural properties bordering INP, especially those located in areas of high environmental fragility (IBAMA, 1999).

Data Analysis

To delimit the sub-basin, images from the ASTER GDEM V2 sensor (NASAJPL, 2009) were used, with a spatial resolution of 30 meters, and contour lines were generated at intervals of 50 m, resulting in a Digital Terrain Model (DTM) (Teske et al., 2014). The Hydrology tool of ArcGIS 10 (ESRI, 2006) was used for the automatic delimitation of the sub-basin, following the methodology described by Trajano et al. (2012).

Assuming there were no alterations in native forest cover within the boundaries of Iguaçu National Park due to its status as a conservation unit, the analyses were applied only to the agricultural matrix of the sub-basin, the surface subject to anthropic intervention. To obtain updated data for future studies, supervised classification was applied to the 2016 image, also, analyses of slope, native forest cover, and landscape metrics were performed.

We determined slope intervals based on thematic maps from the Parana Institute of Economic and Social Development (IPARDES, 1995) to identify physical constraints on implementing agricultural activities. The slope function of ArcGIS 10 was used, and terrain was categorized into intervals: flat to gently undulating terrain (0 to 10%), undulating terrain (10 to 20%), strongly undulating terrain (20 to 45%), and mountainous (> 45%). The percentage of the surface area and the percentage of forest cover per slope interval for the agricultural matrix were obtained.

For the classification of land use and land cover in the agricultural matrix, orbital images corresponding to scenes (orbit/point) 223/077 and 223/078 from the Thematic Mapper (TM) sensor of the Landsat-5 platform (acquisition date: 08/02/1986 and 08/11/2001, false-color RGB-453 composition) and the Operational Land Imager (OLI) sensor of the Landsat-8 platform (acquisition date: 07/03/2016, false-color RGB-564 composition) were used, both with a temporal resolution of 16 days and a spatial resolution of 30 meters (Rezende et al., 2011). All images were obtained from the United States Geological Survey website.

In the process of classifying TM and OLI sensor images, we adopted the supervised method and the Maximum Likelihood (MaxVer) algorithm, which incorporates both the mean spectral values and the variance of the data set (Souza et al., 2013). This classification method requires training samples, called regions of interest (ROIs), defined by the interpreter for the algorithm to perform classification.

We defined land use categories during supervised classification, assuming anthropic use as crops, exposed soil, forestry, water, and urbanized areas. The category called native forest cover included valley bottoms and/or riparian vegetation and native forest fragments. After the classification process, we combined the classes composing each category, generating two macro classes called anthropic use and native forest cover, thus allowing for more precise identification of native forest cover present in the agricultural matrix of the sub-basin (Ribeiro et al., 2009).

We verified the accuracy of the classifications using a sampling point grid, individually developed for the years 1986, 2001, and 2016, in which 50 points were randomly distributed for each of the seven classes, totaling 350 points per year. To estimate the accuracy of the classification, we used the confusion matrix, where omission and commission errors were calculated (Mello et al., 2014; Souza et al., 2013), obtaining the Overall Accuracy (OA) and Kappa (K) indices (FOODY, 2002). Satellite image processing and classification were performed using ENVI software, version 4.8 (SOUZA et al., 2013).

Among the fragments identified in supervised classification, only those with an area greater than three hectares (3 ha) were vectorized (Atlântica, 2016) and categorized into ten size classes (in hectares: 3 to 5; 5 to 10; 10 to 15; 15 to 20; 20 to 25; 25 to 30; 30 to 50; 50 to 100; 100 to 250; 250 to 500). Subsequently, we analyzed the number of fragments and the percentage of forest cover per size class (Ribeiro et al., 2009).

We used the V-LATE extension, Vector-Based Landscape Analysis Tools, version 2.0 beta (Lang & Tiede, 2003), to obtain area, density, size, shape, and proximity indices, for the landscape and size classes. The equations are detailed in Mendes et al. (2015) and Lang and Tiede (2003).

Landscape-scale metrics are generated based on the mean (Lang & Tiede, 2003). The mean Shape Index (MSI in V-Late, or SHAPE_MN in Fragstats) analyzes the shape adjusted to a constant. The closer it is to one, the closer to a circular shape, and the lower the perimeter-area ratio, obtaining equidistant edges from the center of the fragment (Mello et al., 2016).

The mean Fractal Dimension index (MFRACT), calculated from the perimeter-area ratio of natural flat shapes, quantifies their degree of complexity, as it is based on a geometric shape that exhibits structure at all spatial scales. Thus, shapes with simple and straight perimeters approach one, and more complex shapes approach two (Juvanhol et al., 2011). According to Gomide and Lignau (2008), straight-line shapes attribute artificiality to the environment, indicating that the landscape has been subjected to land use planning.

The mean Proximity Index (MPI) is obtained by summing the area of each fragment within the same class, divided by the respective Euclidean distance edge-to-edge, admitting only fragments within the search radius. Therefore, the smaller the sum of the fragment areas (CA) and the greater the distance between them, the lower the value of MPI. The higher the MPI value, the greater the degree of isolation between fragments of the same size class (Lang & Tiede, 2003).

With automatic delineation, we verified that the eastern direct influence area of Iguaçu National Park in the Gonçalves Dias River sub-basin region has a total surface area of 49,522 ha, with 23,106 ha (46.66%) belonging to Iguaçu National Park and 26,417 ha (53.34%) corresponding to the agricultural matrix surface. The landscape of the Gonçalves Dias River sub-basin presents an abrupt transition between the forest cover of the eastern extremity of Iguaçu National Park and the mosaic that makes up the agricultural matrix of the eastern buffer zone.

We found that by 1986, the Gonçalves Dias river sub-basin was already in an advanced fragmentation process. As reported by Ribeiro et al. (2009) and Teixeira et al. (2009), classification based on TM and OLI sensor scenes enabled the identification of fragments with tree structure, present for at least 15 years in the agricultural matrix of the Gonçalves Dias river sub-basin.

In the direct influence area with agricultural matrix surface, supervised classification identified 3,378 ha (OA = 85.33%, K = 82) of native forest cover in the year 1986, representing 12.78% of the total. In the year 2001, we observed 3,401 ha (OA = 89.33%, K = 87%) representing 12.87%, and in the year 2016, 4,158 ha (OA = 90.28%, K = 88%) representing 15.73% of native forest cover (Fig. 2).

According to Roderjan et al. (2002), Paraná had 83% of its territory covered by native vegetation; however, the process of colonization and expansion of agricultural frontiers, more intense in the northern and western regions, resulted in the current scenario, where only 11.7% of its territory maintains remnants of the Atlantic Forest (Atlântica, 2016).

With the analysis of slope on the buffer zone surface, we observed a predominance of flat to gently undulating terrain (10,653.80 ha or 40.33%), followed by undulating terrain (9,147.79 ha or 34.63%), strongly undulating terrain (6,498.20 ha or 24.60%), and only 116.97 ha (0.44%) in mountainous terrain.

We observed the influence of physical restrictions directed by IPARDES (1995) for the implementation of agricultural and forestry activities, as native forest cover showed a larger area on strongly undulating terrain 2,030 ha (49%), followed by undulating terrain 1,321 ha (32%), flat to gently undulating terrain 730.58 ha (17%), and mountainous terrain with only 76.5 ha (2%) of the agricultural matrix in the buffer zone of Iguaçu National Park.

We found that between 0 to 20% slope, corresponding to 74.96% (19,801.59 ha) of the agricultural matrix surface, only 2,052.36 ha (10.36%) of native forest cover were identified. In these areas, a lower rate of native forest cover was expected, considering that the only restriction for land use is the implementation of conservation practices (Borges & Rezende, 2023).

In contrast, when measuring the area located on slopes above 20%, it was found that, together, they correspond to 25.04% of the agricultural matrix (6,615.17 ha), of which 2,106.24 ha (31.84%) maintain native forest cover. There is a total restriction for mechanized agriculture on slopes, and even non-mechanized agriculture could only be admitted under moderate to severe restrictions.

Only 116.97 ha of surface area was identified in mountainous terrain (above 45%), however, only 76.41 ha maintain native forest cover, exposing a deficit of 40.56 ha. This deficit exposes probable areas for the restoration of native vegetation cover, as according to the new Forest Code (BRASIL, 2012), slopes or areas where the gradient exceeds 45% are designated as permanent preservation areas (PPAs), rendering them ineligible for exploitation or certain land use activities under environmental regulations.

In addition to physical restrictions, these areas highlight generally shallow soils (IPARDES, 1995), which can enhance erosive processes and degradation throughout the entire watershed (Rodrigues et al., 2011), negatively altering the quantity, shape, and quality of water resources offered upstream (Tucci & Mendes, 2006).

After vectorization, the native vegetation identified in the agricultural matrix in the Landsat image of 2016 depicted 204 native forest fragments, totaling 4,158.60 ha (15.74% of the total sub-basin area). The indices generated in V-LATE for the size classes of the fragments are grouped in Table 1.

Table 1

Landscape ecology indices for fragment size classes in the agricultural matrix of the Gonçalves Dias river sub-basin. Abbreviations: CA (Total area of fragments); MPS (Mean patch size); PSSD (Standard deviation of patch size); PSCoV (Coefficient of variation of patch size); MSI (Mean shape index); MFRACT (Mean fractal dimension); MPI (Mean proximity index).
Size classes (ha)	CA area (ha)	Number of fragments	Density and size			Shape		MPI proximity
			MPS (ha)	PSSD (ha)	PSCoV (%)	MSI	MFRACT
3 a 5	260.3	68	3.83	0.54	14.09	2.07	1.38	0.65
5 a 10	299.57	44	6.81	1.38	20.31	2.28	1.37	0.22
10 a 15	287.52	24	12.4	1.26	10.13	2.50	1.37	0.36
15 a 20	327.07	19	17.21	1.54	8.93	2.83	1.38	0.95
20 a 25	222.12	10	22.21	1.62	7.29	3.30	1.40	0.40
25 a 30	211.77	8	26.47	1.25	4.73	3.12	1.38	0.23
30 a 50	453.04	11	41.19	6.41	15.58	3.27	1.38	4.53
50 a 100	883.59	13	67.97	13.33	19.62	3.72	1.38	1.29
100 a 250	941.54	6	156.92	31.08	19.81	4.37	1.38	10.02
250 a 500	262.08	1	262.08	0.00	0.00	4.56	1.38	0.00

In the eastern direct influence area with agricultural matrix, fragments with an area below 50 ha (n = 186) contribute to 91% of the total number of fragments and 50% of the native forest cover (2,087.81 ha), while forest fragments with an area larger than 50 hectares (n = 18) contribute only 9% of the total fragments and correspond to 50% of the total area (2,087 ha) (Fig. 3).

The quantity obtained in this study corroborates with the results of Ribeiro et al. (2009), Juvanhol et al. (2011), Pirovani et al. (2014), Azevedo, Gomes, and Moraes (2016), Mello et al. (2016), which found a higher representation of fragments with an area smaller than 50 ha in studies in the Atlantic Forest.

The fragmentation process is closely linked to the expansion of agricultural frontiers, mechanization, and anthropization (Mello et al., 2016; Silva et al., 2016). As a consequence of changes in the matrix, alterations occur in the internal environments of the fragments and in the canopy composition.

In Atlantic Forest fragments, especially those with an area of less than 10 ha, the canopy is dominated by a small number of pioneer or opportunistic gap trees; this dominance increases with decreasing fragment size, resulting in the disappearance of the emergent layer in the smaller, older fragments (Tabarelli et al., 2002).

At the landscape scale, the mean shape index (MSI) was 2.59, the proximity index (MPI) was 1.05, and the mean fractal dimension index (MFRACT) was 1.38. Similar to findings by Mello et al. (2016), in the Gonçalves Dias river sub-basin, larger fragments tend to exhibit greater complexity in their shape, and the mean fractal dimension index (MFRACT) shows that the landscape of the sub-basin is composed of fragments of moderately complex forms.

Our value of the mean fractal dimension index (1.38) was similar to other studies conducted in the Atlantic Forest, such as those obtained by Pirovani et al. (2014) in the Itapemirim River basin, Espírito Santo (between 1.36 and 1.40), and by Azevedo et al. (2016), who obtained 1.32 in the Buranhém River basin, extreme south of Bahia.

Gomide and Lingnau (2008) obtained an average fractal dimension index of 1.10 for fragments located in the APA do Iraí, Curitiba, Paraná, the same value obtained by Juvanhol et al. (2011) for the ecological corridor between the Forno Grande and Pedra Azul State Parks, Espírito Santo.

The average degree of isolation between fragments (MPI) showed variation among size classes. We observed a higher degree of isolation among fragments belonging to the "3 to 5 ha" class (MPI = 0.65) than among the "5 to 10" (MPI = 0.22), "10 to 15" (MPI = 0.36), "20 to 25" (MPI = 0.40), and "25 to 30" (MPI = 0.23) classes.

As fragmentation progresses and promotes habitat loss, reducing the original area of the fragments, the remaining small fragments become more accessible to hunting and timber exploitation. Similarly, the percentage of forest under edge effects increases, leading to the establishment of ruderal species, further exacerbating habitat loss (Tabarelli et al., 2002).

Field studies in the Atlantic Forest have accumulated evidence of synergy among phenomena correlated with habitat loss, fragmentation, edge effects, forest product exploitation, elimination of disperser species, and the frequency of forest fires (Castro et al., 2021; Lacerda et al., 2022; Scussel et al., 2020).

During the analyzed period (1986-2001-2016), we observed an increase in native forest cover in the direct eastern influence area of the Iguaçu National Park. However, the area exhibits a high degree of fragmentation, with few fragments larger than 50 hectares, which represent approximately 50% of the forest cover.

In the last period studied, we found that the shapes of the fragments are moderately complex. Additionally, we observed that smaller fragments still have less complex shapes, as they are relatively young areas, indicating that the regeneration of these areas was planned.

On the other hand, larger fragments have greater shape complexity, highlighting the need for their preservation, as they can serve as seed sources for areas that still need to be restored.

We found that in the last year of the analysis, there was still a deficit of forest cover of 40.47 hectares in mountainous areas, i.e., permanent preservation areas where the slope exceeds 45%. In this condition, we suggest that forest restoration measures be taken, as these areas are not subject to exploitation.

The fragmentation of the direct influence area of the Iguaçu National Park in the Gonçalves Dias river sub-basin is likely the result of the historical process of predominantly agricultural land use, guided by the few physical restrictions of the terrain.

Funding Declaration

This study was financed in part by the Coordenação de Aperfeiçoamento de Pessoal de Nível Superior – Brasil (CAPES) – Finance Code 001.

Author Contribution

LGT and HMM conceived and designed the research; HMM installed the experiment and collected the data. BSF, HMM, VHRP and EM analyzed the data; all autors interpreted the results. HMM and BSF wrote the paper, with contributions of the co-authors.

Acknowledgement

We would like to thank Capes for the scholarships awarded to the first and second authors, CNPq for the scholarship awarded to the third author, and the Laboratory of Topography and Geoprocessing of the State University of Western Paraná, Cascavel campus. The authors also thank Gabriela Gariani Quinto for the thorough review of the journal's guidelines. This study was financed in part by the Coordenação de Aperfeiçoamento de Pessoal de Nível Superior – Brasil (CAPES) – Finance Code 001.

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Forest Fragmentation Dynamics in the Direct Influence Area of Iguaçu National Park, Brazil

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