Artificial Perches: Ecological and Functional Aspects of its Contribution in the Atlantic Forest

Abstract

Ecological restoration through conventional plantation techniques can create forests with low biodiversity. As such, one way to overcome possible shortcomings of the restoration process is to use nucleation techniques, such as artificial perches. These structures attract the avifauna and increase the deposition of seeds associated with feces or bird regurgitation. Seed rain and seedlings regeneration were monitored under artificial perches and control areas in a degraded area of Rio de Janeiro, RJ, Brazil. In this study, 46 morphospecies of seeds were identified. Under the perches, greater abundance and richness of seeds were found with certain ecological and functional traits that support the role of artificial perches as a biological diversity core. Seedling establishment was low under the perches and control areas. This suggests that integrated actions to improve soil conditions should be applied to enhance seedling establishment.

Keywords:
ecological restoration; nucleation; seed rain

1. INTRODUCTION

Ecological restoration is the assisting process of restoration of a degraded, damaged or destroyed ecosystem (SER, 2017). It is a deliberate activity that initiates or accelerates environmental recovery, with respect to its health, integrity and sustainability. In this way, restoration actions aim to develop ecologically viable communities, protecting and promoting the natural change within the ecosystem, as well as sustainability and resiliency (SER, 2017). Degradation occurs when the natural habitat conversion leads to loss of adaptability to chemical, physical and biological characteristics (Ibama, 1990; Lamb et al., 2005).

Most of the areas originally covered by Atlantic Forest were destroyed as a result of land conversion into rural areas and urban expansion (Ribeiro et al., 2009). The Atlantic Forest is composed of a series of ecosystems along the Brazilian east coast, ranging from mangroves and restingas to altitude forests and rugged terrain (Mittermeier, 2004). The high rate of biological diversity and endemic species, coupled with high level of degradation, make this environment one of the top hotspots for biodiversity conservation in the world (Laurance, 2009; Myers et al., 2000). The Atlantic Forest currently has about 15.2% of its original vegetation cover, considering the native forest remnants larger than 3 ha (SOS Mata Atlântica & Inpe, 2018). These remnants, in most cases, are insufficient for the conservation of many rare species, especially those that require large areas (Ribeiro et al., 2009).

In this scenario, the state of Rio de Janeiro, located in Southeastern Brazil, suffers from forest cover loss, leading to instability of the slopes, which in turn leads to erosion and landslides (Figueiró & Coelho Netto, 2007). Important areas such as Maciços do Gericinó-Mendanha, Tijuca and Pedra Branca suffer heavy environmental degradation because of deforestation and disordered occupation on their slopes (Barbosa & Rodrigues, 2017).

Environmental degradation can cause losses in the structure and diversity of species, creating temporary or permanent reduction in the productive capacity of an ecosystem (Moraes et al., 2010). The process of forest recovery may vary; more stable areas tend to recover quickly, while in other areas it may take centuries (Bechara et al., 2016). This is closely linked to the concept of ecological resilience of the area (Moraes et al., 2010). The process of succession is often self-establishing, but in cases where degradation is very intense, it is necessary to intervene with long-term strategies (Kageyama et al., 2008; Sansevero et al., 2017).

Alternative techniques of ecological restoration are an effective alternative to overcome some of the shortcomings of conventional planting methods used in ecological restoration projects (Bechara et al. 2007; Franks 2003; Yarranton & Morrison, 1974). These techniques aim to create microhabitats and nuclei that act as facilitators for arrival of species and survival of all life forms, accelerating ecological succession and increasing diversity of adjacent areas (Bechara et al., 2016; Reis et al., 2003).

One nucleation technique is the construction of artificial perches that can be used by birds for foraging, resting and shelter. This causes a greater deposition of zoochorous seeds associated with stool and regurgitation (Holl, 1998; Stiles & White, 1986) or the unintentional fall of seeds under these perches. This is one of the best strategies to connect forest fragments, since it promotes an ecological flux from the animal-plant interactions, and has the potential to connect landscape units in different directions (Tres & Reis, 2009). However, the efficiency of this technique is still not clear; even if the perches contribute in attracting birds and enriching seed rain, little is known about the ecological and functional traits of these seeds and whether the arrival of propagules would be effective in plant establishment (Helleman et al., 2012; Holl, 1998; Reid & Holl, 2013).

Based on the considerations aforementioned, this study aims to quantify and qualify the propagule arrival and the initial seedling establishment with the use of artificial perches and without perches (control) in an area of Atlantic Forest slope, under restoration process. The specific objectives were: (1) to identify morphospecies through seeds; (2) to quantify the abundance and richness, (3) to assess ecological and functional traits of the morphospecies, (4) to quantify the seedling abundance; and (5) to evaluate the results of the method at different distances (30 and 60 m) of the forest remnant.

MATERIAL AND METHODS

Study area

The Inhoaíba mountain is located near the Pedra Branca Massif, in the West Zone of Rio de Janeiro, RJ (Figure 1). The climate is tropical hot and humid, with annual average rainfall of 1187 mm and rainfall seasonally defined with small water deficiency between the months of July and October (Togashi et al., 2012). The mean annual temperature is 26ºC (Oliveira et al., 1980; Rio de Janeiro, 2000). The original vegetation of the study area is Dense Ombrophylous Forest (Mata Atlântica strictu sensu), mainly submontane forest (Veloso et al., 1991). The area already underwent some restoration attempts, without success. The area is covered by a mosaic of vegetation in initial and intermediate stages of succession and presents moderate susceptibility to erosion.

Figure 1
Location of the Rio de Janeiro state (a), Rio de Janeiro municipality (b), Campo Grande neighborhood (c), and reforestation area in Serra de Inhoaíba (d).

Installation of artificial perches and sampling points

Ten artificial perches were mounted, with 30 m in-between. Five were arranged 30 m away from the reforestation area and the other five at 60 m. These perches were made with 7 m high bamboo stems. In each stem, circular frame sticks (1 m × 30 mm) were fixed in the heights of 3.5 m and 5.5 m, using ropes and epoxy mass. Each perch was buried 1 m deep with the use of an auger, to avoid tipping the structure.

Below each perch two square collectors of 0.50 × 0.50 m were allocated, made with wire and mousseline fabric, for a total catch area of 0.50 m². Still below the perches, 1.0 × 0.50 m plots were allocated for the monitoring of the seed germination that eventually reached the site. In each subplot of 0.50 × 0.50 m, the following treatments were carried out: one with grass management and the other without management (Figure 2). In the management treatment, all grass cover was removed in each survey. Five meters from each perch, a seed collector that was considered the control was installed.

Figure 2
Scheme of seedling sampling and seed rain.

Monitoring of seed rain and seedling regeneration

The seed rain and seedling establishment were monitored for six months (April to September 2015), in ten expeditions. The collected seeds were stored in paper bags and dried in the laboratory in a stove for 48 hours or until they had a constant dry weight.

The seeds were sorted and identified using a stereoscopic microscope then counted and assigned to morphospecies. The following functional and ecological traits were assessed for each morphospecies: successional stage (tolerant and intolerant to shade) (Whitmore, 1990), dispersion syndrome (anemochorous, autochorous and zoochorous) (Van der Pijl, 1982) liana or grass (Radford et al., 1974), and origin (exotic, native or naturalized) (Moro et al., 2012). Seed mass was weighted on an scale (to mg), and the mean mass of each morphospecies was calculated and classified as light (mean mass < 0.001 g), medium (0.001 g < mean mass < 0.015 g) or heavy (mean mass ≥ 0.015 g).

Seedlings using aluminum blades with individual numbers were monitored. In each visit, death and entry of new individuals were recorded.

Statistical analyses

A cluster analysis was performed using Euclidean distances with complete linkage between the areas, on a presence-absence matrix with seed richness data. Then the richness and abundance of seed morphospecies were compared through a t-test, when the assumptions for parametric analysis were met. In this case, the areas with perches at 30 m and 60 m of the remnant were compared with the control areas. The Kolmogorov-Smirnov tests for non-parametric distributions were used. In the seedlings case, and when the parametric assumptions were respected, they were compared with an Anova factorial test with two fixed factors (presence of perches and grass management), using the Tukey’s posterior test. When these assumptions were not met, the non-parametric Friedman analysis was used. These analyses were performed using the Statistica 7 software (StatSoft, 2004). All grass species were excluded from seed richness and abundance analysis because these seeds were deposited in the collectors by the wind, a common process in graminoid fields such as the experiment area.

RESULTS AND DISCUSSION

Seed rain

In total, this study found 27,700 seeds of 46 morphospecies from 20 families (Table 1). All 46 morphospecies were under the perches and 21 morphospecies at the control groups. The Poaceae family contributed with 22,949 seeds (82%), mainly grasses dispersed by wind. The high number of grass seeds deposited over the six months may be related to the predominant matrix characteristic (“Colonião” grass - Urochloa maxima (Jacq.) RDWebster) and the collection period in the dry season, when anemochorous species are favored (Howe & Smallwood, 1982). Thus, we analyzed the data excluding this family, and from the remaining 4,750 seeds, 4,238 (89%) were collected under the perches and 512 seeds (11%) in the controls.

Table 1
Seed species deposited on perches and control groups in São Jorge, Rio de Janeiro, RJ. The species were classified according to the successional stage, dispersion, habit and origin: intolerant (I), shade tolerant (T), zoochorous (Z), autochorous (Aut), anemochorous (Ane), shrub (Arb), arboreal (Arv), herbaceous (H), subshrub (Sarb), liana (L), native (N), naturalized (Nz), exotic (E).

Family	Species	Succession	Dispersion	Habit	Origin
Amaranthaceae	Amaranthaceae	I			N
Anacardiaceae	Schinus terebinthifolius Raddi	I	Z	Arb/Arv	N
Asteraceae	Bidens pilosa L.	I	Z	H	Nz
	Mikania stipulacea Willd.	I	Ane	H	N
	Parthenium hysterophorus L.	I	Aut	H	Nz
	Helianthus annuus L.	I	Z/Aut	H	E
	Synedrellopsis grisebachii	I	Z/Aut	H	Nz
	Trichogonia sp	I		Arb/Sarb	N
	Hypocaeris radicata ou Porophyllum ruderale	I	Z/Aut	H	E
Caryophyllaceae	Silene gallica L.	I	Ane/Aut	H	Nz
Chloranthaceae	Hedyosmum cf.		Z	Arb/Arv	N
Eritroxylaceae	Erythroxylum sp.		Z	Arb/Arv	N
Fabaceae	Crotalaria mucronata Desv.	I	Z/Aut	H	N
	Dalbergia nigra (Vell.) Allemão ex Benth.	I	Ane	Arv	N
	Crotalaria anagyroides Kunth.	I	Z/Aut	Arb	N
	Aeschynomene indica L. ou Calopogonium	I	Z/Aut	H
	Fabaceae
Lamiaceae	Leucas martinicensis (Jacq.) R. Br.	I	Aut	H	Nz
Meliaceae	Guarea macrophylla Vahl	T	Z	Arv	N
Myrtaceae	Campomanesia	T	Z	Arb/Arv	N
Papillionaceae	Desmodium adscendens (Sw). DC.	I	Z	Sarb	Nz
Passifloraceae	Turnera subulata Sm.	I	Z/Aut	Arb	N
Piperaceae	Piper cernuum ou divaricatum	I	Z	Arb	N
Poaceae	Axonopus scoparius (Flügge) Kuhlm	I	Ane	H	N
	Brachiaria plantaginea (Link) Hitchc	I	Ane	H	E
	Chloris gayana Kunth	I	Ane	H	N
	Echinolaena inflexa (Poir.) Chase	I	Z/Ane	H	N
	Pennisetum pedicelatum Trin.	I	Ane	H	N
	Hyparrhenia rufa (Nees) Stapf.			H	E
	Sorghum arundinaceum ou Chloris polydactyla (L.) Sw	I	Ane	H	N
Rubiaceae	Alseis sp.			Arb/Arv	N
	Psychotria sp.		Z		N
	Psychotria ou Palicourea		Z	Arb/Arv	N
Rutaceae	Dictyoloma vandellianum A.Juss.		Ane	Arv	N
Salicaceae	Casearia sylvestris Sw	I	Z	Arb	N
	Casearia commersoniana Cambess.	I	Z	Arb	N
	Casearia (oblongifolia ou selloana)		Z	Arb/Arv	N
Solanaceae	Solanum americanum Mill.	I	Z	H	N
	Solanum paniculatum L.	I	Z	Arb	N
Vitaceae	Cissus cf. erosa	I	Z	L	N
Undetermined	undetermined 1
	undetermined 2
	undetermined 3
	undetermined 4
	undetermined 5
	undetermined 6

In a study in the closest adjacent forest fragment, Muler (2014) reported only three species found in our study (Casearia commersoniana Cambess., Dalbergia nigra (Vell.) Allemão ex Benth. and Schinus terebinthifolius Raddi). This suggests that the seeds come from more distant fragments, highlighting that this type of contribution can create greater species richness and genetic diversity, which are important issues and great challenges for restoration projects (Lamb et al., 2005; Zuchi et al., 2017).

We compared our results to those of Vicente et al. (2010), a study carried out in the Atlantic Forest of southern Brazil, and we found that seed abundance was eight times higher, and richness was doubled. This suggest that our study area shows great potential for seed arrival. Other studies in southern Brazil found 21,864 seeds of 51 morphospecies (Tomazi et al., 2010) and, in Porto Rico, 21,507 seeds of 28 morphospecies (Shiels and Walkers, 2003). These studies collected seeds for more than one year.

In the clustering analysis, this study observed one group formed by the control sample, and other formed by the perches, with the exception of one perch sample point (p10) (Figure 3). However, there was no clustering when the distance of the sampling in relation to the fragment edge was considered (Figure 3). That is, the perch distance from the forest edge was not a main factor in the seed species composition. In a similar experiment, in pasture near a fragment of Atlantic Forest in the state of Paraná, Zwiener et al. (2014) reported significant differences in the seed rain richness on isolated trees and artificial perches installed at 10 m and 300 m from the forest edge, with greater species richness at more remote perches. Dias et al. (2014) did not find difference in the seed species composition in perches installed between 5 m and 35 m from the fragment edge, a similar result to the one observed in this study.

Figure 3
Dendrogram of dissimilarity using Euclidean distance with complete linkage for perches and controls samples at different distances in relation to forest fragment (P1 to P5 and C1 to C5 to 30 m and P6 to P10 and C6 to C10 to 60 m) in Serra de Inhoaíba, Rio de Janeiro, Brazil.

Abundance under the perches was nine times greater than the one observed in the control group (Perches, median: 448.5; Control: 53; Z = 3.3, p ≤ 0.00). The richness was also higher in perches (Perches: 13.0 ± 2.44, Control: 4.9 ± 2.18, F ≤ 60.94, p ≤ 0.00, Figure 4). This difference was observed in other studies with artificial perches, confirming the richness and abundance increase hypothesis (Almeida et al., 2016; Bechara, 2007; Bochese et al., 2008; Dias et al., 2014; Guidetti et al., 2017, Oliveira et al., 2018).

Figure 4
Box plot representing the richness of seed rain on perches (P) and the control group (C). Mean, standard deviation and confidence interval are plotted.

Regarding the ecological and functional traits, we observed a difference between seeds under perches and the control sample (Table 2), evidence of the potential of perches to contribute as biological diversity nuclei (Reis et al., 2003; Tres & Reis, 2009). We only found shade-tolerant species under perches. Shade-tolerant species generally have longer life cycle and are typically part of forest in more advanced successional stages (Durigan et al., 2008). In the tree species seeds case, 104 (23%) arrived under perches, while only one (0.19%) arrived in the control group. In restoration projects, trees are an important component of soil cover, as they increase environmental heterogeneity and create microhabitats for germination, consequently favoring forest regeneration (Brown & Lugo, 1994; Melo & Durigan, 2007). We recorded 6% heavy seeds under perches and 0.8% in the control group. Large-sized seeds may represent higher establishment capacity, but can also represent arrival difficulties in areas in regeneration due the disappearance of potential dispersers (Dalling & Hubbell, 2002; Lamb et al., 2005). Under the perches, this study found that 88.1% of the seeds were native while in the control group this percentage was 53.3% (Table 2). The high number of native species in a seed bank may strengthen the vegetation recovery potential (Silva-Weber et al., 2012).

Table 2
Quantitative data for successional stage, origin and seeds habit collected in controls and perches.

		Successional stage			Origin			Habit
	Total	Intolerant	Tolerant	Native	Exotic	Naturalized	Herbaceous	Shrub	Tree
Controls	512	473	0	273	0	194	292	180	2
Perches	4238	4013	96	3735	17	411	607	3236	157

• We recorded 1,233 zoochorous seeds under perches and only eleven in the control group. In a similar experiment, also in Rio de Janeiro, Dias et al. (2014) found in 21 collection days, 118 times more zoochorous seeds in perches than in the control group. Artificial perches formed new seed nuclei within the pasture area, acting as nucleating points in the degraded area, facilitating zoochorous seed arrival (Almeida et al., 2016; Tomazi & Castellani, 2016). Zoochorous seeds under perches represent mostly arboreal life forms, suggesting that the birds with an arboreal food habit bring seeds of nearby forest fragments (Tres & Reis, 2009). Such facts demonstrate that perches can serve as ecological trampolines connecting landscape elements (Tres & Reis, 2009).

Seedlings

The seedling numbers recorded throughout this experiment were small, with low establishment numbers and high death rates for all treatment types. There were no significant differences of these variables between perches and the control sample, or with and without grass management (Table 3), because of the low values observed. In general, invasive grasses with populations in disequilibrium (high abundance and density) may be an exclusion factor for seed germination (Moraes et al., 2010; Parker, 1997). However, our results suggest that establishment and mortality are not caused by grass competition, but rather to inadequate conditions for seed germination and seedling establishment. Factors such as water stress, mechanical damage, herbivory, pathogens, soil compaction, among others, affect seedling establishment and survival in pasture environments (Bocchese et al., 2008).

Table 3
Mortality and establishment of seedlings in perch and control plots with and without grass management.

Treatment		Mortality	Friedman	Establishment Fatorial Anova
Perches	Management	0.35 ± 0.26	2.41; p = 0.49	1 ± 4.37	Factor 1: treatment F = 0.38; p = 0.54
	Without Management	0.3 ± 0.2		2.5 ± 1.23	Factor 2: management F = 0.44; p = 0.51
Control Plots	Management	0 ± 0		0.1 ± 0.32	Interaction: F = 0.38; p = 0.54
	Without Management	0 ± 0		0 ± 0

Similar results with low seed germination and seedling establishment were observed in other experiments with perches in tropical pastures (Almeida et al., 2016; Heelemann et al., 2012; Holl, 1998), suggesting that factors such as soil degradation can interfere in the germination of the dispersed seeds and in the survival of germinated individuals. Holl (1998) observed in an experiment with perches in Costa Rica that the number of seedlings was extremely low and did not differ significantly between habitat types (open pasture and perches). Although the perches help seed arrivals in open areas, due to the conditions of these sites, they have little chance of surviving (Almeida et al., 2016; Heelemann et al., 2012; Reid & Holl, 2013). This suggests that seed arrival does not guarantee the seedlings establishment and that the tropical forests recovery demands integrated actions, with issues still remaining to be solved.

CONCLUSION

Artificial perches increased the morphospecies richness and abundance in the seed rain in the Serra de Inhoaíba, Rio de Janeiro, RJ, Brazil. Forest fragment distance (30 m and 60 m) did not influence seed arrival. Artificial perches assist the dispersion of zoochorous, large-seeded and shade-tolerant species, important ecological and functional traits in the restoration of communities’ ecological processes. However, these species showed low seedling establishment and high seedling mortality. Other ecological restoration techniques that complement artificial perches should be used in order to overcome the obstacles after dispersal. Integrated strategies that aim to increase seedling establishment and improve soil quality can help in the catalysis of this process.

ACKNOWLEDGEMENTS

To the teams at Secretaria de Meio Ambiente of the city of Rio de Janeiro, the Projeto Mutirão and the Fundação Bio-Rio for the financial and logistical support. To the members of the Laboratório de Ecologia Florestal of Universidade Federal do Estado Rio de Janeiro and the Reflora project for the technical and logistical support in all steps of this research. To the researchers Dr. Richieri Sartori for the contribution in project design and Dr. Arno F. N. Brandes, for the review of the manuscript.

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Publication Dates

• Publication in this collection
  17 Apr 2020
• Date of issue
  2020

History

• Received
  20 June 2018
• Accepted
  30 Mar 2019