CAROLINA A. LEÓN1*, GISELA OLIVÁN-MARTÍNEZ2, JUAN LARRAÍN3,5 Y
REINALDO VARGAS4
Botanical Sciences
94 (3): 441-453, 2016
DOI: 10.17129/botsci.555
Universidad Bernardo O
Higgins, Centro de Investigación en Recursos Naturales
y Sustentabilidad, Santiago,
Chile.
2
Departamento de Biología
Vegetal I, Facultad de Ciencias Biológicas, Universidad
Complutense de Madrid,
Madrid, España.
3
Science & Education, The
Field Museum, Chicago IL,
U.S.A.
4
Departamento de Biología,
Universidad Metropolitana
de Ciencias de la Educación,
Santiago, Chile
5
Instituto de Biología, Facultad de Ciencias, Pontificia
Universidad Católica de
Valparaíso, Campus Curauma, Valparaíso, Chile.
*Corresponding autor: carolina.leon@ubo.cl.
1
Abstract
Bryophytes and lichens are an important component of biodiversity. Nevertheless, these cryptogamic
groups are rarely included in floristic and ecological studies in southern South America. We present the
first comparison of patterns of alpha and beta diversity of bryophytes and macrolichens in peatlands and
Tepualia stipularis forests (TF) on Isla Grande de Chiloé, Chile. Two kinds of Sphagnum peatlands were
studied, which were defined according to their origin and their vegetation, natural peatlands (GP) and anthropogenic peatlands (AP). A total of 86 species were found: 42 liverworts, 29 mosses and 14 lichens. The
most species-rich sites were AP with a total of 52 species, followed by TF with 45 species, and GP with 21
species. The total bryo-lichenic diversity reported in this study was considerably higher than that reported
in other studies for Patagonian peatlands. The three types of studied habitats showed significant differences
in species richness and diversity indices. We found clear distinctions between the three habitat types, with
significant differences in the floristic composition of GP, AP, and TP. Moreover, AP presented a species
composition that has not been previously documented in TF or GP. They are the result of human action,
but do not depend on continued human intervention for their maintenance. Therefore, here we propose to
denominate AP as a novel ecosystem.
Keywords: biodiversity patterns, emerging ecosystem, liverworts, macrolichens, mosses, Chile.
Patrones de diversidad de briófitos y liquenes en turberas y bosques de Tepualia
stipularis en Patagonia norte (Chile): evidencia de un ecosistema emergente en el
sur de Sudamérica
Resumen
Los briófitos y líquenes son un componente importante de la biodiversidad. Sin embargo, estos grupos
criptogámicos son escasamente incluidos en estudios ecológicos y florísticos en el Sur de Sudamérica. En
este estudio se presenta la primera comparación de patrones de diversidad alfa y beta de briófitos y macrolíquenes en turberas y bosques de Tepualia stipularis (TF) de la Isla Grande de Chiloé, Chile. Se estudiaron
dos tipos de turberas esfagnosas, las cuales fueron definidas de acuerdo a su origen y vegetación, turberas
naturales (GP) y turberas antropogénicas (AP). En este estudio se reporta un total de 86 especies, de las
cuales 42 fueron hepáticas, 29 musgos y 14 líquenes. Los sitios con mayor riqueza de especies fueron los
AP (52 especies), seguidos por TF con 45 especies y GP con 21 especies. La diversidad brio-liquénica reportada en este estudio es considerablemente más alta en relación a lo reportado en otros estudios para las
turberas patagónicas. Los tres tipos de hábitats analizados mostraron diferencias significativas en riqueza
de especies e índices de diversidad. Además, se encontraron claras diferencias en la composición florística
de GP, AP, y TP. AP presentó una composición de especies que no había sido previamente documentada
en TF o GP. Esta nueva conformación es el resultado de la acción antrópica sobre estos lugares, pero no
dependen de la intervención humada para su mantenimiento. En consecuencia, proponemos denominar a
AP como ecosistemas noveles.
Palabras clave: ecosistemas emergentes, hepáticas, macrolíquenes, musgos, patrones de biodiversidad,
Chile.
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CarolINa a. leóN eT al.
B
ryophytes and lichens are an important component of biodiversity (Rozzi et al. 2008) and play
a key role in ecosystems such as peatlands (Minayeva 2008). Some of them, specifically Sphagnum spp., have been considered ecosystem engineers. These organisms directly or indirectly
modulate the availability of resources to other species and, additionally, they modify, maintain
and/or create habitats (Jones et al. 1994). Moreover, the ground layer in peatlands is dominated
by a 90-100 % cover of bryophytes (Vitt & Belland 1995) and the functions of the peatland
ecosystem is highly dependent on this layer. For instance, nutrient sequestration, water-holding
abilities, decomposition, and acidification are all influenced by this layer (Vitt 2000). Nevertheless, these cryptogamic groups are rarely included in floristic and ecological studies (Pharo et
al. 1999, Lang et al. 2009). Southern South America is no exception.
Vast expanses of peatland can be found in Chilean Patagonia. A significant number of peatlands were formed by peat accumulation in open water after glacial retreat (Heusser 1984,
Villagrán 1988, Villagrán 1991), referred to here as glaciogenic peatlands (GP). However, in
northern Patagonia, the use of fire and clearcutting since the middle of the 19th century in places
with low drainage have created areas of wetlands dominated by species of the genus Sphagnum
l. (Zegers et al. 2006, Díaz et al. 2008). When Tepualia forests (TF), characterized by poor
drainage, are burned or cleared, waterlogged conditions hinder forest recolonization and stimulate Sphagnum colonization (Díaz et al. 2007, Díaz & Silva 2012). These habitats are called
anthropogenic peatlands (AP).
Besides, TF are swamp habitats, closely related to peatlands. This type of forest is dominated
by Tepualia stipularis (Hook. & Arn.) Griseb. (Myrtaceae), and can be associated with Podocarpus nubigenus Lindl. (Podocarpaceae), Pilgerodendron uviferum Florin. (Cupressaceae) and/or
Drimys winteri J. R. Forst. & G. Forst. (Winteraceae). It grows in waterlogged areas (García &
Ormazabal 2008) and accumulates organic matter (Veblen & Schlegel 1982). Several studies
show that peatlands and TF have been linked by their floras demonstrating that the vascular and
bryophytic floras of these habitats are highly similar (Villagrán & Barrera 2002, Villagrán et
al. 2002, Villagrán et al. 2003, Villagrán et al. 2005). Díaz et al. (2008) reported differences in
floristic composition that allow to distinguish between GP (natural) and AP. However, there are
no comprehensive studies that quantify and compare the floristic composition of AP, GP, and TF.
Another connection is that these ecosystems are seriously threatened. Peatlands are threatened
and degraded because peat extraction and Sphagnum harvesting, mainly to use as a substrate in
horticulture (Díaz & Silva 2012). In Chile, Sphagnum exports increased by over 400 % between
2002 and 2011 (ODEPA 2016). TF are also threatened because their firewood is one of the main
energy sources on the island (Neira & Bertin 2010).
We are studying AP as an ecosystem that has been shaped by human activity. Its transformation of landscape has caused changes to biological communities, posing new challenges for
traditional thinking in conservation and resource management (lindenmayer et al. 2008). Taking into account this changes in ecosystem-human relation, Milton (2003) presented a novel
concept of emerging ecosystems. This concept defines an ecosystem whose species composition
and relative abundance have not previously occurred within a given biome. The key characteristics of these ecosystems are: new species combinations, with the potential for changes in
ecosystem functioning, and they are the result of deliberate or inadvertent human action, but do
not depend on continued human intervention for their maintenance (Hobbs et al. 2006). Under
this concept we wonder, if AP is a novel or an emerging ecosystem?
In this research, we study alpha and beta diversity of mosses, liverworts, and lichens in AP,
GP, and TF of Isla Grande de Chiloé (Chile). In particular, we address the following questions:
i) Are there significant variations in species composition between the studied habitat types? ii)
Are AP more floristically related to TF? iii) Do GP (natural habitats) have a higher bryo-lichenic
diversity than AP? iv) Is there evidence to recognize AP as a novel ecosystem?
Methods
Study Site. The study area was located in the Isla Grande de Chiloé, los lagos region, Chile
(42°-43° S and 73°-75° W). The prevailing climate is wet temperate with a strong oceanic influence (di Castri & Hajek 1976). The total annual rainfall is about 2,300 mm (CONAF 2009),
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BryopHyTe aNd lICHeN dIversITy IN paTaGoNIaN BoGs
Figure 1. location of studied
site in Chiloé. Glaciogenic
peatlands (GP) (black circles):
PL, Púlpito; CA, Caulles; and
RN, Rio Negro. Anthropogenic peatlands (AP) (gray
circles): SD, Senda Darwin;
CH, Chepu; PM, Pumanzano;
lC, lecam and TG, Teguel.
Tepualia forests (TF) (white
circles): CU, Chiloé National
Park and SDB, Senda Darwin
forest.
73º 30’S
74º 00’S
SD/SDB
42º 00’S
LC
RN
PM
CH
CA
TG
42º 30’S
CU
PL
43º 00’S
reaching 5,000-6,000 mm in some areas, with a mean summer temperature of 10.2 ºC and a
mean winter temperature of 6.2 ºC (Pérez et al. 2003).
We selected ten sites located in the northern and central parts of the island (Figure 1). Two
kinds of Sphagnum peatlands were studied, which were defined according to their origin and
their characteristic vegetation (Díaz et al. 2008). Three study sites represented the glaciogenic
peatland type (GP): Río Negro (GP-RN), Los Caulles (GP-CA) and Púlpito (GP-PL); five study
sites represented the anthropogenic peatland type (AP): Senda Darwin (AP-SD), Lecam (APLC), Pumanzano (AP-PM), Río Chepu (AP-CH) and Teguel (AP-TG). In addition, two sites
represented the Tepualia forest type (TF): Chiloé National Park (TF-CU) and another area of
Senda Darwin (TF-SDB) (Figure 1).
Species composition. On each site we established three lineal transects of 50 m. In each transect,
three equidistant sample plots were placed. We extracted a block from the surface layer measuring 20 × 20 × 10 cm from each sample plot. These blocks were used to evaluate species richness
and biomass, following Bullock’s harvest method (1997). Dry biomass was used to estimate
species abundance for each sample plot. Specimens were carefully determined according to
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CarolINa a. leóN eT al.
morphological characters, and their characteristics were compared with the literature (Engel
1978, Schuster 2000, Schuster 2002, Larraín 2007, Buck & Goffinet 2010), type specimens
or other herbarium specimens deposited in PC, S, MACB and CONC herbaria. For lichens,
chemical characters were also used. Lichen substances were identified using thin layer chromatography (TLC), following the protocol of White & James (1985). Specimens were deposited in
MACB and CONC herbaria.
Although Drosera uniflora Willd. is a vascular plant, its presence was registered due to its
great significance as an indicator of GP species. Due to their tiny size, the liverworts Calypogeia sphagnicola, Cephalozia skottsbergii and Hyalolepidozia bicuspidata were considered as a
functional group. likewise, the lichens Cladonia pycnoclada, C. mitis and C. arbuscula subsp.
squarrosa were considered as the subgenus Cladina following Ruoss and Ahti (1989), because
chemical tests are required for correct determination. Appendix 1 includes a list with the collected species.
Data analysis. Alpha diversity was evaluated in two scales following Gray’s (2000) concepts:
point species richness (SRP), the species richness of a single sampling unit (quadrant); and sample species richness (SRS), the species richness of a number of sampling units from a site of a
defined area (site). In addition, we calculated the Shannon diversity index (H’) and evenness (J’)
to combine the effects of species richness and abundance (Magurran 2004). To assess changes
in species composition among habitat types, we calculated beta diversity using the Bray-Curtis
dissimilarity index (Bray & Curtis 1957). Moreover, cluster analysis was performed using the
unweighted pair group metric with averaging method (UPGMA) and Bray-Curtis presence/absence distance to evaluate the resemblance among sites. Non-metric multidimensional scaling
(NMDS) was used to compare plant communities from AP, GP, and TF. Relative abundance
and Bray–Curtis distance was used as a general measure of ecological similarity for NMDS
ordination (Beilman 2001). Analysis of similarities (ANOSIM) was used to test for differences
in species composition for the three habitat types. R values of ANOSIM were generated using
9,999 random permutations. We used the Non-Parametric Kruskal–Wallis H ANOVA to test
significant differences in the richness and diversity measures among habitats and sites.
We employed PAST (Hammer et al. 2001) for indices, cluster analysis, NMDS and ANOSIM.
STATISTICA 7.0 (StatSoft 2004) for the Kruskal-Wallis H test.
Results
alpha Diversity. A total of 86 species was found: 42 liverworts, 29 mosses, 14 lichens and one
insectivorous flowering plant. Fifty three-point five percent (53.5 %) of the species were found
at only one site and are here considered potentially rare within the studied peatlands: 16 mosses,
21 liverworts and 9 lichens. AP had a total of 52 species (18 mosses, 21 liverworts and 13 lichens), TF had 45 species (15 mosses, 29 liverworts and 1 lichen), and GP had 21 species (4
mosses, 13 liverworts and 3 lichens) (Figure 2). Of the 86 species, 29 were only found in TF, 27
were exclusive of the AP and five occurred only in GP. Nevertheless, we found shared species
between habitat types, nine species between AP and GP, nine species between AP and TF, six
species between TF and GP, and seven species that were shared among the three habitats.
Table 1. Species richness and diversity index by habitat type. SRP, point species richness; SRS, sample species
richness; p: mean per cuadrant, s: richness or index per type of habitat. (*) significant differences (p < 0.001,
Kruskal-Wallis test) among habitat types. Anthropogenic peatlands (AP), glaciogenic peatlands (GP), and
Tepualia forests (TF).
AP
GP
TF
SR p total *
5
4.6
10.6
SRS total
52
21
45
Shannon index p*
0.62
0.49
1.28
Shannon index S
1.64
0.89
2.86
Evenness p*
0.39
0.32
0.57
Evenness S
0.41
0.29
0.75
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BryopHyTe aNd lICHeN dIversITy IN paTaGoNIaN BoGs
20
Mosses
10
Species richness
Figure 2. Species richness
of mosses, liverworts, and
lichens, in the three habitat
types. Anthropogenic peatlands (AP), glaciogenic peatlands (GP) and Tepualia forests (TF).
30
Liverworts
20
10
20
Lichens
10
AP
GP
TF
SRP, SRS and diversity indices were significantly different among the three habitat types. TF
showed the highest SRP and diversity index, while AP presented the highest SRS (Table 1).
Species richness and abundance were significantly different between study sites (Figure 2 y 3).
SRS ranged between 7 and 34 species where AP-SD and TF-CU were the highest, and AP-LC
and GP-RN the lowest. SRP ranged between 2 and 14 species per quadrant. Diversity indices
followed the same trends in species richness where AP-SD, TF-SDB and TF-CU had the highest
values. Nevertheless, AP-PM and AP-PL presented the lowest diversity indices.
When analyzing the SRS per botanical groups, it was seen that AP-SD and TF-SDB had
the highest number of mosses, TF-CU the most liverworts and AP-TG and AP-SD the most
lichens.
Beta Diversity. Dendrogram of floristic composition based on Bray-Curtis similarity clearly
shows two groups of habitats with a similarity of over 30 % (Figure 4). The first group included
three locations, TF-SDB and TF-CU (both TF, which had a similarity of 48 %, and AP-SD,
100
90
Relative abundance (%)
Figure 3. relative species
abundance of mosses, liverworts, and lichens in the three
habitat types. Anthropogenic
peatlands (AP), glaciogenic
peatlands (GP) and Tepualia
forests (TF).
80
70
60
50
40
30
20
10
AP
GP
Mosses
Liverworts
445
TF
Lichens
94 (3): 441-453, 2016
CarolINa a. leóN eT al.
Figure 4. Bray-Curtis similarity dendrogram of floristic
composition among studied
habitats. Tepualia forests (+):
TF-CU, Chiloé National Park
and TF-SDB, Senda Darwin
forest. Anthropogenic peatlands (*): AP-CH, Chepu; APLC, Lecam AP-PM, Pumanzano; AP-SD, Senda Darwin;
and AP-TG, Teguel. Glaciogenic peatlands (**): GP-CA,
Caulles; GP-PL, Púlpito; and
GP-RN, Rio Negro.
0.1
0.2
0.3
0.4
0.5
0.6
0.7
0.8
0.9
1
SDB+
CU+
SD*
LC*
TG*
PM*
CH*
RN**
PL**
CA**
which is a sister site of the clade formed by these sites. The second group included the seven
remaining locations. In this group, AP-LC and AP-TG were individually separated and subgrouped with a similarity of 45 %. Within this sub-group, two subclusters were formed: GP-RN,
GP-PL and GP-CA, which have a similarity of 60%, and AP-PM and AP-CH with a similarity
of 58 %.
Based on non-metric multidimensional scaling (NMDS), the structure in species composition
revealed differences in the habitat type (Figure 5). In this plot we can see a clear separation of TF
Figure 5. Non-parametric
multidimensional scaling ordination representing similarity in bryophyte and lichen
species composition between
habitat types. Black diamonds
represent anthropogenic peatlands (AP), grey hexagons
glaciogenic peatlands (GP),
and white circles Tepualia
forests (TF) (n = 90).
0.18
0.15
0.12
0.09
0.06
0.03
0
-0.03
-0.06
-0.09
-0.2
-0.15
-0.1
-0.05
446
0
0.05
0.1
0.15
0.2
0.25
94 (3): 441-453, 2016
BryopHyTe aNd lICHeN dIversITy IN paTaGoNIaN BoGs
samples (white circles), while AP (black diamonds) are arranged in a dispersed form in the plot
and not distantly separated from GP (grey hexagons). AP and GP samples are closer than TF.
The statistical significance of differences in abundance and species composition among habitats was confirmed by the ANOSIM tests (RANOSIM global = 0.412, p = 0.0001). When ANOSIM
pair-wise comparisons were performed, we detected that TF vs. AP (p = 0.0001; RANOSIM =
0.770) and GP vs. TF (p = 0.0001; RANOSIM = 0.930) were significantly different in species composition; however, AP vs. GP (p = 0.3453; RANOSIM = 0.012) were more closely related.
Discussion
Cryptogamic diversity. Bryophyte and lichen diversity have repeatedly been underestimated
due to limited knowledge of these groups, especially in southern South America. Indeed,
our research demonstrates the importance of these groups as our results show that the total bryophyte and lichen diversity were considerably higher than that previously reported
from Patagonian peatlands. Díaz et al. (2008) reported 27 species of bryophytes and lichens
in peatlands of Chiloé, Villagra et al. (2009) recorded five species of terricolous lichens in
Sphagnum peatlands of Aisén, and Kleinebecker et al. (2010) found 54 bryo-lichenic species
in the peatlands of Magallanes. In our study, 56 species of bryophytes and lichens were reported for peatlands of Chiloé (AP and GP). Under these circumstances, in a diversity context,
the peatlands of Los Lagos Region are as rich as the peatlands of Magallanes, which have
been considered significantly important due to their location. The Magallanes Region reports
the highest diversity of bryophytes and lichens in the country (Goffinet et al. 2006). On the
other hand, if the number of species recorded in this study is compared with species found in
bogs of the Northern Hemisphere, for instance, Canada with 36 species (Vitt & Belland 1995)
or Britain with 39 species (Wheeler 1993), the diversity observed in our study shows great
relevance. This is especially remarkable because the peatlands of the Southern Hemisphere
are under-represented compared to the vast percentage of land they occupy in the Northern
Hemisphere (Joosten & Clarke 2002).
Differences between habitats. our results also showed differences in species richness, composition and diversity indices among study sites and among types of studied habitats (Table 1). This
trend is more evident in the AP group, as seen in the cluster analysis (Figure 4). This analysis
Table 2. Species richness and diversity index by sites. SRP, point species richness; SRS, sample species richness; p, mean per cuadrant; s, richness
or index per type of habitat. Tepualia forests: TF-CU, Chiloé National Park and TF-SDB, Senda Darwin forest. Anthropogenic peatlands: AP-CH,
Chepu; AP-LC, Lecam AP-PM, Pumanzano; AP-SD, Senda Darwin; and AP-TG, Teguel. Glaciogenic peatlands: GP-CA, Caulles; GP-PL, Púlpito;
and GP-RN, Rio Negro. (*) significant differences (p < 0.001, Kruskal-Wallis test) among sites.
AP
GP
TF
AP-CH
AP-LC
AP-PM
AP-SD
AP-TG
GP-CA
GP-PL
GP-RN
TF-CU
TF-SDB
SR p total*
4.7
2.1
4.3
7.3
6.4
5.6
4.6
3.7
13.8
7.4
SRS total
14
7
10
34
22
15
16
9
32
27
SR p mosses*
2.7
1.8
1.6
3.9
2.2
1.8
1.3
1.4
3.2
3.7
6
4
2
13
7
4
2
3
7
14
SRS mosses
SR p liverworts*
1.7
0.3
2.2
2.2
1.8
2.4
2.2
1.8
10.1
3.8
SRS liverworts
5
3
5
14
6
8
11
4
24
13
SR p lichens*
0.3
0
0.6
1.2
2.4
1.3
1
0.4
0.4
0
3
0
3
7
9
2
2
1
1
0
SRS lichens
SRS insectivorous
Shannon index p*
0
0
0
0
0
1
1
1
0
0
0.61
0.35
0.30
1.07
0.78
0.63
0.37
0.47
1.50
1.07
Shannon index S
1.26
0.74
0.42
2.00
1.61
1.03
0.59
0.82
2.43
2.45
Evenness p*
0.37
0.42
0.20
0.55
0.41
0.37
0.22
0.36
0.57
0.57
Evenness S
0.48
0.38
0.18
0.57
0.52
0.38
0.21
0.37
0.7
0.74
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shows that GP and TF form delimited groups and have less within-group variability, while
AP are more heterogeneous. These differences could be related to processes carried out in the
cryptogamic community establishment, and the chemical and topographic characteristics of the
sites. For instance, AP-SD has greater similarity to TF and this similarity could be attributed to
its early stage of formation. In this locality, the peat layer was the smallest of the sampled sites
and is located very close to the forest. Moreover, it could be labeled as an ecotonal zone between
the forest and peatland. Another highlighted example is AP-LC, which is part of the AP and GP
cluster; however, it is the first to diverge from the group. This site has particular hydrological
characteristics (león et al. In review) because the water level is very high and not significantly
lower in summer; something that does not happen in any of the other study sites. Furthermore,
the highest richness, diversity index and number of exclusive species were observed in AP. In
contrast, GP showed the lowest values of these community parameters. TF showed a high richness, independent of the scale (point or sample), and this habitat type presented a large number
of exclusive species. These results can be understood by their phytogeographic location. TF
form part of the temperate forest of Chile, an ecosystem that has been classified as a biodiversity
hotspot for conservation of global significance by its uniqueness and high threats (Myers et al.
2000). Moreover, in NMDS (Figure 5) and ANOSIM analyses, we could also see clear differences among the three habitat types. There were significant differences in the floristic composition of GP, AP, and TF, where GP and AP were more closely related to each other because they
share a large number of species and environmental characteristics. on the contrary, TF were
distantly related to the other two groups. The significant differences between AP and GP in floristic composition concurred with Díaz et al. (2008) who described differences in floristic composition between GP (natural) and AP. Nonetheless, the clear differences between the flora of
peatlands and TF reported in this research differs from previously published studies (Villagrán
& Barrera 2002; Villagrán et al. 2002; Villagrán et al. 2003; Villagrán et al. 2005) that suggest
that the flora of peatlands and TF are similar.
Novel ecosystems, ecosystem services and implication for management. According to our results, AP have very distinct and singular characteristics. They are characterized by high values
of diversity (Table 1), with a large number of endemic species of southern South America (León
et al. 2014). Moreover, new records for the bryophyte flora of the island and Chile have been
found (león et al. 2013). In addition, even when all species growing in AP belong to the Valdivian ecoregion and it is not possible to attribute them to other biomes, these ecosystems show
a singular composition of species that did not previously occur when they were TF (before
clearcutting). These new species combinations have the potential to change ecosystem functions, as discussed below. They are the result of human action, but do not depend on continued human intervention for their maintenance. According to Hobbs et al. (2006), these are all
characteristics that define a novel ecosystem. Therefore, applying the concepts of Hobbs et al.
(2006) and Milton (2003), we can denominate AP as a novel ecosystem. In these novel ecosystems, the new species compositions have deeply changed the landscape of the island and ecosystem services. Díaz & Armesto (2007) showed that Sphagnum cushions could act as a nursery
species, facilitating the establishment of embothrium coccineum. Nevertheless, these cushions
could inhibit the establishment of pioneer species such as Drimys winteri and Baccharis patagonica in successional scrubs of Chiloé, which is a limiting factor for forest regeneration. on
the other hand, the colonization and the establishment of large populations of Sphagnum in
sites where the forest was removed have also changed ecosystem functioning. León & Oliván
(2014) found that AP are accumulating peat and therefore are also acting as carbon sinks and
reservoirs of freshwater; ecosystem services relevant to the island. It is important to highlight
that the peatlands of Chiloé are threatened and degraded by Sphagnum harvesting, especially
AP. Unfortunately, Chile has no legal regulation for the extraction of Sphagnum moss. These
sites have been excessively exploited without sustainable protocols, and as a consequence, they
show evident signs of overexploitation. This imposes the need to promote conservation and
restoration of these ecosystems. However, three important questions arise and require a deeper
analysis: What would be the direction of the restoration in AP? Would it be to recover the temperate rainforest (historical setting)? Or would it be to recover telmatic wetlands formed after a
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disturbance? These are significant points of discussion about the conservation and management
of these emerging ecosystems, because in many parts of the world, primary motivations for ecosystem management are associated with human survival rather than considerations of historic
fidelity (Hobbs et al. 2009). In this case, considering their high social and economic value, a
focus on ecosystem functions rather than recomposition of species (historical) or the cosmetics
of landscape surfaces would be useful according to Choi (2007). A reasonable way would be to
promote the growth of Sphagnum and to restore the ability to store water and peat. This would
have a significant impact on local communities because Chiloé peatlands are very important for
fresh water supply on the island. This island has no freshwater input from snowmelt as found
on mainland Chile; the freshwater input is mainly from precipitation (Zegers et al. 2006). Thus,
according to the climate change scenario, low rainfall rates in recent years means that freshwater on the island is at risk and the conservation of peatlands is of even more importance to the
population.
Finally, we do not know about the dynamics of species composition under new abiotic conditions, especially Sphagnum species, which are ecosystem engineers. Therefore, it is necessary
to increase efforts to understand their functioning and the main environmental factors driving
these ecosystems. Moreover, these studies could provide insights into the effects that global
change factors can have on these novel ecosystems, and could provide important information
for management and ecological restoration.
Acknowledgements
This research was supported by grants AECID A/025081/2009, Cooperación al Desarrollo
UCM 4138114 and AECID A/030011/2011. We are very grateful to Alfonso Benítez-Mora for
his assistance in the field. We wish to thank the Fundación Senda Darwin, Aserradero A.R.P.,
Chepu adventures, I. Municipalidad de Dalcahue and CONAF Chiloé for their logistic support
during field work. C. A. León acknowledges the support of the doctoral fellowship provided by
CoNICyT-Gobierno de Chile.
This is a contribution to the Research Program of LTSER-Chile network at Senda Darwin Biological Station, Chiloé, Chile.
Literature cited
Beilman D.W. 2001. Plant community and diversity change due to localized permafrost dynamics in bogs
of western Canada. Canadian Journal of Botany 79:983-993.
Bray J.R. and Curtis J.T. 1957. An ordination of the upland forest communities of Southern Wisconsin.
ecological Monographs 27:325-349.
Buck W.R. and Goffinet B. 2010. Preliminary key to the mosses of Isla Navarino, Chile (Prov. Antártica
Chilena). Nova Hedwigia 138:215-229.
Bullock J. 1996. Plants. In: Sutherland W. J. Ed. Ecological census techniques: a handbook, pp. 186-213,
Cambridge University Press, New York.
CONAF [Corporación Nacional Forestal] 2009. Plan de Gestión Territorial, Plan de Acción Provincial.
Corporación Nacional Forestal/Oficina Provincial Chiloé, Castro.
Choi Y.D. 2007. Restoration ecology to the future: a call for new paradigm. Restoration ecology 15:351353.
di Castri F. and Hajek E.R. 1976. Bioclimatología de Chile. Universidad Católica de Chile, Santiago.
Díaz M.F. and Armesto J.J. 2007. Limitantes físicos y bióticos de la regeneración arbórea en matorrales
sucesionales de la Isla Grande de Chiloé, Chile. Revista Chilena de Historia Natural 80:13-26.
Díaz M.F., Bigelow S. and Armesto J.J. 2007. Alteration of the hydrologic cycle due to forest clearing and
its consequences for rainforest succession. Forest ecology and Management 244:32-40.
Díaz M.F., Larraín J., Zegers G. and Tapia C. 2008. Caracterización florística e hidrológica de turberas de
la Isla Grande de Chiloé, Chile. Revista Chilena de Historia Natural 81:455-468.
Díaz M.F. and Silva W. 2012. Improving harvesting techniques to ensure Sphagnum regeneration in Chilean peatlands. Chilean Journal of agricultural Research 72:296-300.
Engel J.J. 1978. A taxonomic and phytogeographic study of Brunswick Peninsula (Strait of Magellan)
Hepaticae and Anthocerotae. Fieldiana Botany 41:1-319.
García-Berguecio N. and Ormazabal-Pagliotti C. 2008. Árboles Nativos de Chile. Enersis S.A, Santiago.
449
94 (3): 441-453, 2016
CarolINa a. leóN eT al.
Goffinet B., Rozzi R., Lewis L., Buck W. and Massardo F. 2012. los bosques en miniatura del Cabo de
Hornos: ecoturismo con lupa. University of North Texas – Ediciones Universidad de Magallanes,
Punta Arenas.
Gray J.S. 2000. The measurement of marine species diversity, with an application to the benthic fauna of
the Norwegian continental shelf. Journal of experimental Marine Biology and ecology 250:23-49.
Hammer Ø., Harper D.A.T. and Ryan P.D. 2001. PAST: Paleontological Statistics Software Package for
Education and Data Analysis. Palaeontologia electronica 4:art. 4.
Heusser C.J. 1984. Late-Glacial-Holocene Climate of the Lake District of Chile. Quaternary Research
22:77-90.
Hobbs R.J., Arico S., Aronson J., Baron J.S., Bridgewater P., Cramer V.A., Epstein P.R., Ewel J.J., Klink
C.A., Lugo A.E., Norton D., Ojima D., Richardson D.M., Sanderson E.W., Valladares F., Vilà M.,
Zamora R. and Zobel M. 2006. Novel ecosystems: theoretical and management aspects of the new
ecological world order. Global ecology and Biogeography 15:1-7.
Hobbs R.J., Higgs E. and Harris J.A. 2009. Novel ecosystems: implications for conservation and restoration. Trends in ecology & evolution 24:599-605.
Jones C.G., Lawton J.H. and Shachak M. 1994. Organisms as Ecosystem Engineers. Oikos 69:373-386.
Joosten H. and Clarke D. 2002. Wise use of mires and peatlands. Background and principles including a
framework for decision-making. International Mire Conservation Group & International Peat Society,
Saarijärvi.
Kleinebecker T., Hölzel N. and Vogel A. 2010. Patterns and gradients of diversity in South Patagonian
ombrotrophic peat bogs. austral ecology 35:1-12.
Lang S.I., Cornelissen J.H.C., Hölzer A., Ter Braak C.J.F., Ahrens M., Callaghan T.V. and Aerts R. 2009.
Determinants of cryptogam composition and diversity in Sphagnum-dominated peatlands: the importance of temporal, spatial and functional scales. Journal of ecology 97:299-310.
Larraín J. 2007. Musgos (Bryophyta) de la estación biológica Senda Darwin, Ancud, isla de Chiloé: lista de
especies y claves para su identificación. Chloris chilensis Año 10: <http://www.chlorischile.cl>
León C.A., Gaxiola A. and Oliván G. In review. Is the origin of peatlands a key factor that affects the species composition? evidence from peatlands of northern Chilean Patagonia. Submitted to ecosystems
Journal.
León C.A. and Oliván G. 2014. Recent Rates of Carbon and Nitrogen Accumulation in peatlands of Isla
Grande de Chiloé-Chile. Revista Chilena de Historia Natural 87:26.
León C.A., Oliván G., Larraín J., Vargas R. and Fuertes E. 2014. Bryophytes and lichens in peatlands and
Tepualia stipularis forest of Isla Grande de Chiloé-Chile. anales del Jardín Botánico de Madrid 71:e003.
León C.A., Oliván G. and Pino-Bodas R. 2013. New records for the Chilean bryophyte and lichen flora.
Gayana Botánica 70:241-246.
Lindenmayer D.B., Fischer J., Felton A., Crane M., Michael D., Macgregor C., Montague-Drake R., Manning A. and Hobbs R.J. 2008. Novel ecosystems resulting from landscape transformation create dilemmas for modern conservation practice. Conservation letters 1:129-135.
Magurran A.E. 2004. Measuring biological diversity. Blackwell Science, Oxford.
Milton S.J. 2003. ‘Emerging ecosystems’ - a washing-stone for ecologists, economists and sociologists?
South african Journal of Science 99:404-406.
Minayeva T. 2008. Peatlands and Biodiversity. In: Parish F., Sirin A., Charman D., Joosten H., Minayeva
T., Silvius M. and Stringer L. Eds. assessment on peatlands, biodiversity and climate change: main report, pp. 60-97, Global Environment Centre, Kuala Lumpur and Wetlands International, Wageningen.
Myers N., Mittermeier R.A., Mittermeier C.G., da Fonseca G.A.B. and Kent J. 2000. Biodiversity hotspots
for conservation priorities. Nature 403:853-858.
Neira E. and Bertin R. 2010. Hábitos del uso de leña en Castro, Isla de Chiloé. Revista Bosque Nativo
45:3-8.
ODEPA. 2016. Exportaciones de musgos secos, distintos de los usados para ramos y adornos y de los
medicinales. Código SACH 14049020. <http://www.odepa.cl/series-anuales-por-producto-de-exportaciones-importaciones/> (accessed august 8, 2016)
Pérez C.A., Armesto J.J., Torrealba C. and Carmona M.R. 2003. Litterfall dynamics and nitrogen use efficiency in two evergreen temperate rainforests of southern Chile. austral ecology 28:591-600.
Pharo E.J., Beattie A.J. and Binns D. 1999. Vascular Plant Diversity as a Surrogate for Bryophyte and
Lichen Diversity. Conservation Biology 13:282-292.
Rozzi R., Armesto J.J., Goffinet B., Buck W., Massardo F., Silander J., Arroyo M.T.K., Russell S., Anderson C.B., Cavieres L.A. and Callicott J.B. 2008. Changing lenses to assess biodiversity: patterns of
species richness in sub-Antarctic plants and implications for global conservation. Frontiers in ecology
and the environment 6:131-137.
Ruoss E. and Ahti T.T. 1989. Systematics of some reindeer lichens (Cladonia subg. Cladina) in the Southern Hemisphere. lichenologist 21:29-44.
450
94 (3): 441-453, 2016
BryopHyTe aNd lICHeN dIversITy IN paTaGoNIaN BoGs
Schuster R.M. 2000. Austral Hepaticae Part I. Nova Hedwigia, Beiheft 118, J. Cramer, Berlin.
Schuster R.M. 2002. Austral Hepaticae Part II. Nova Hedwigia Beiheft 119, J. Cramer, Berlin.
StatSoft. 2004. STATISTICA for Windows, user’s guide (version 7.0) StatSoft Inc., Tulsa.
Veblen T. and Schlegel F.M. 1982. Reseña ecológica de los bosques del sur de Chile. Bosque 4:73-115.
Villagra J., Montenegro D., San Martín C., Ramírez C. and Álvarez I. 2009. Estudio de la flora liquénica
de las turberas de la Comuna de Tortel (región de Aisén), Patagonia chilena. anales del Instituto de la
Patagonia 37:53-62.
Villagran C. 1988. Late quaternary vegetation of southern Isla Grande de Chiloé, Chile. Quaternary Research 29:294-306.
Villagran C. 1991. Historia de los bosques templados del sur de Chile durante el Tardiglacial y Postglacial.
Revista Chilena de Historia Natural 64:447-460.
Villagrán C. and Barrera E. 2002. Musgos del archipiélago de Chiloé, Chile. Corporación Nacional Forestal - Gobierno de Chile, Puerto Montt.
Villagrán C., Barrera E., Cuvertino J. and García N. 2003. Musgos de la Isla Grande de Chiloé, X Región,
Chile: Lista de especies y rasgos fitogeográficos. Boletín del Museo Nacional de Historia Natural,
Chile 52:17-44.
Villagrán C., Barrera E. and Medina C. 2002. Las Hepáticas del Archipiélago de Chiloé, Chile. Corporación Nacional Forestal - Gobierno de Chile, Puerto Montt.
Villagrán C., Hässel de Menéndez G. and Barrera E. 2005. Hepáticas y Antocerotes del Archipiélago de
Chiloé. Una introducción a la flora briofítica de los ecosistemas templados lluviosos del sur de Chile.
Corporación de Amigos del Museo Nacional de Historia Natural, Santiago.
Vitt D.H. 2000. Peatlands: ecosystems dominated by bryophytes. In: Shaw A. J. and Goffinet B. Eds. Bryophyte biology, pp. 312-343, Cambridge University Press, Cambridge.
Vitt D.H. and Belland R.J. 1995. The bryophytes of peatlands in continental western Canada. Fragmenta
Floristica et Geobotanica 40:339-348.
Wheeler B.D. 1993. Botanical diversity in British mires. Biodiversity and Conservation 2:490-512.
White J. and James P.W. 1985. A new guide to microchemical techniques for the identification of lichen
substances, Bulletin of the British Lichen Society No. 57, London.
Zegers G., Larraín J., Díaz M.F. and Armesto J.J. 2006. Impacto ecológico y social de la explotación
de pomponales y turberas de Sphagnum en la Isla Grande de Chiloé. Revista ambiente y Desarrollo
22:28-34.
451
94 (3): 441-453, 2016
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Appendix 1. Occurrence (X) of species in anthropogenic peatlands (AP), glaciogenic peatlands
(GP) and Tepualia forests (TF) of North Patagonia.
Species
Anthropogenic Glaciogenic Tepualia
peatlands
peatlands
forests
Mosses
Acrocladium auriculatum (Mont.) Mitt.
Breutelia subplicata Broth.
Campylopus acuminatus Mitt.
Campylopus introflexus (Hedw.) Brid.
Campylopus pyriformis (Schultz) Brid.
Dicranella circinata Herzog
Dicranoloma billarderii (Brid.) Paris
Dicranoloma imponens (Mont.) Renauld
Dicranoloma robustum (Hook. f. & Wilson) Paris
Distichophyllum dicksonii (Hook. & Grev.) Mitt.
Dendrohypopterygium arbuscula (Brid.) Kruijer
Eucamptodon perichaetialis (Mont.) Mont.
Hymenodontopsis mnioides (Hook.) N. E. Bell,
A. E. Newton & D. Quandt
Hypopterygium didictyon Müll. Hal.
Hypnum chrysogaster Müll. Hal.
Hypnum cupressiforme var. mossmanianum (Müll.
Hal.) Ando
Pohlia nutans (Hedw.) Lindb.
Polytrichastrum longisetum (Sw. ex Brid.) G. L. Sm.
Ptychomniella ptychocarpa (Schwägr.) W. R. Buck et al.
Ptychomnion cygnisetum (Müll. Hal.) Kindb.
Rhaphidorrhynchium callidum (Mont.) Broth.
Rigodium brachypodium (Müll. Hal.) Paris
Rigodium pseudothuidium Dusén
Sphagnum capillifolium (Ehrh.) Hedw.
Sphagnum falcatulum Besch.
Sphagnum fimbriatum Wilson
Sphagnum magellanicum Brid.
Sphagnum cf. subsecundum Nees
Liverworts
Anastrophyllum schismoides (Mont.) Stephani
Balantiopsis asymmetrica (Herzog) J. J. Engel
Balantiopsis cancellata (Nees) Stephani
Bazzania peruviana (Nees) Trevis.
Calypogeia sphagnicola (Arnell & J. Perss.) Warnst.
& Loeske
Cephalozia skottsbergii Steph.
Cheilolejeunea cf. obtruncata (Mont.) Solari
Chiloscyphus attenuatus (Stephani) J. J. Engel
& R. M. Schust.
Chiloscyphus breutelii (Gottsche) J. J. Engel
& R. M. Schust.
Chiloscyphus horizontalis (Hook.) Nees
Chiloscyphus magellanicus Steph.
Chiloscyphus striatellus C. Massal.
Cryptochila grandiflora (Lindenb. & Gottsche) Grolle
452
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
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BryopHyTe aNd lICHeN dIversITy IN paTaGoNIaN BoGs
Appendix 1. Continuation.
Species
Anthropogenic Glaciogenic Tepualia
peatlands
peatlands
forests
Frullania cf. boveana C. Massal.
Herbertus runcinatus (Taylor) Kuhnem.
Hyalolepidozia bicuspidata (C. Massal.) S.W.
Arnell ex Grolle
Jamesoniella colorata (Lehm.) Spruce ex Schiffn.
Kurzia setiformis (De Not.) J. J. Engel & R.M. Schust.
Lepicolea ochroleuca (Spreng.) Spruce
Lepidogyna menziesii (Hook.) R. M. Schust.
Lepidozia chordulifera Taylor
Lepidozia fuegiensis Steph.
Leptoscyphus huidobroanus (Mont.) Gottsche
Plagiochila chonotica Taylor
Plagiochila hookeriana Lindenb.
Plagiochila lechleri Gottsche
Plagiochila lophocoleoides Mont.
Plagiochila rubescens (Lehm. & Lindenb.) Lindenb.
Plagiochila subpectinata Besch. & C. Massal.
Porella subsquarrosa (Nees & Mont.) Trevis.
Radula decora Gottsche ex Steph.
Riccardia amnicola Hässel
Riccardia alcicornis (Hook. f. & Taylor) Trevis.
Riccardia floribunda (Stephani) A. Evans
Riccardia hyalitricha Hässel
Riccardia prehensilis (Hook. & Taylor) C. Massal.
Riccardia rivularis Hässel
Riccardia spinulifera C. Massal.
Saccogynidium australe (Mitt.) Grolle
Schistochila lamellata (Hook.) Dumort.
Telaranea blepharostoma (Stephani) Fulford
Telaranea plumulosa (Lehm. & Lindenb.) Fulford
Lichens
Cladia terebrata (Laurer) S. Parnmen & Lumbsch
Cladonia arbuscula (Wallr.) Flot.
Cladonia bellidiflora (Ach.) Schaer.
Cladonia gracilis subsp. elongata (Wulfen) Vain.
Cladonia lepidophora Ahti & Kashiw.
Cladonia scabriuscula (Delise) Leight.
Cladonia squamosa (Scop.) Hoffm.
Cladonia P. Browne subgen. Cladina
Cladonia subsubulata Nyl.
Hypogymnia subphysodes (Kremp.) Filson
Usnea sp.
Peltigera polydactylon (Neck.) Hoffm.
Parmotrema reticulatum (Taylor) M. Choisy
Pseudocyphellaria faveolata (Delise) Malme
Insectivorous plants
Drosera uniflora Willd.
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
453
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