Canopy gaps characteristics and structural dynamics in a natural unmanaged oriental beech (Fagus orientalis Lipsky) stand in the north of Iran

Document Type: Research Paper

Authors

1 Semnan University

2 Gorgan University

3 Research Institute of Forests and Rangelands Tehran

Abstract

Canopy gaps are one of the most important structural features of forest ecosystems, and studying of them can have useful results and implications for forest management. The aim of this study is investigation of characteristics and regeneration within canopy gaps in an intact beech stand in the Shastkalateh Experimental Forest of Hyrcanian region, north of Iran. All canopy gaps and related forest parameters were measured within a permanent plot 16ha. Considering the composition of the forest, the dominant tree species was oriental beech with 36.3% of the stem number and 56.6% of the stand volume. In total 54 canopy gaps were identified which covered about 5% of the forest area. An average of 4.32 gaps.ha-1 existed in the permanent plot and gap sizes varied from 48.3 to 622.7m2. More than three-quarters (77.7%) of canopy gaps were smaller than ≤200m2. Also more than half of the gaps (53%) were formed by a single tree-fall event and beech made up 52% of gap makers and 23.4% of gap fillers. Beech had the second largest proportion on standing deadwood of gap maker in the study area, while velvet maple was the most frequent gap filler in approximately 30% of the gaps. Despite the high frequency of small gaps 100m2, their proportion of the overall gap area reached only 25% that suggests the important role of intermediate and large gaps in the gap dynamics. Considering the recent occurring disturbances in the Hyrcanian Forests, the study analyzed the main characteristics of disturbance regime with the emphasis on the role of wind and longevity of trees. In general, findings of this study showed that the creating small and average gaps in intact beech forests could be based on natural disturbance regimes, And suitable conditions provides for successful regeneration of beech forests in close to nature silviculture.

Keywords


[Research]

Dynamics of canopy gap characteristics in a natural unmanaged oriental beech (Fagus orientalis Lipsky) stand in the north of Iran

M. Amiri1*, R. Rahmani2, Kh. Sagheb-Talebi2, H. Habashi3

1. Dept. of Forestry for Arid Regions, Faculty of Desert Studies, Semnan University, semnan, Iran

2. Dept. of Silviculture and Forest ecology, Faculty of Forest Sciences, Gorgan University of Agricultural Sciences and Natural Resources, Gorgan, Iran

3. Forest Research Division, Research Institute of Forests and Rangelands, Tehran, Iran

* Corresponding author’s E-mail:amiri.mojtaba@yahoo.com

(Received: Oct. 27.2014. Accepted: Apr. 8.2015)

ABSTRACT

Canopy gaps are one of the most important structural features of forest ecosystems, and studying of them can have useful results and implications for forest management. The aim of this study is investigation of characteristics and regeneration within canopy gaps in an intact beech stand in the Shastkalateh Experimental Forest of Hyrcanian region, north of Iran. All canopy gaps and related forest parameters were measured within a permanent plot 16ha. Considering the composition of the forest, the dominant tree species was oriental beech with 36.3% of the stem number and 56.6% of the stand volume. In total 54 canopy gaps were identified which covered about 5% of the forest area. An average of 4.32 gaps.ha-1 existed in the permanent plot and gap sizes varied from 48.3 to 622.7m2. More than three-quarters (77.7%) of canopy gaps were smaller than ≤200m2. Also more than half of the gaps (53%) were formed by a single tree-fall event and beech made up 52% of gap makers and 23.4% of gap fillers. Beech had the second largest proportion on standing deadwood of gap maker in the study area, while velvet maple was the most frequent gap filler in approximately 30% of the gaps. Despite the high frequency of small gaps 100m2, their proportion of the overall gap area reached only 25% that suggests the important role of intermediate and large gaps in the gap dynamics. Considering the recent occurring disturbances in the Hyrcanian Forests, the study analyzed the main characteristics of disturbance regime with the emphasis on the role of wind and longevity of trees. In general, findings of this study showed that the creating small and average gaps in intact beech forests could be based on natural disturbance regimes, And suitable conditions provides for successful regeneration of beech forests in close to nature silviculture.

Key words: Canopy gap, Oriental beech, Permanent Plot, Hyrcanain forests


INTRODUCTION

Forests dominated by oriental beech (Fagus orientalis Lipsky) as a major species are one of the most widespread and abundant vegetation types in the Hyrcanian Forest (Resaneh et al. 2011; Sagheb-Talebi & Schütz, 2002; Sagheb-Talebi et al. 2004). In the other hand, intact oriental beech stands provide a unique opportunity to study the disturbance regimes of forest ecosystems without human influence [4]. In many forest ecosystems, major disturbances are pivotal in controlling the structure of stands within the context set by environmental factors and the present species (Whit 1979; Pickett et al. 1989; Wimberly & Spies, 2000). Disturbance is a permanent feature of forest ecosystems, determining species' composition, structure and process (Atiwil, 1994; Ulanova, 2000; McCarthy, 2001; Kucbel et al. 2010) and it plays a crucial role in the forest ecosystem dynamics (Kucbel et al. 2010). Disturbance events range from the small scale disturbance of single tree-falls or crown-breaks to the large-scale disturbance caused by e.g. catastrophic windstorms. One of the most important disturbances in forest ecosystems is opening areas called “canopy gap”. Canopy gaps play an important role in the regeneration of forest by providing habitat for regenerating seedlings and saplings in the forest floor (Hubbell & Foster, 1996). In many forests throughout the world, tree- fall gaps, opening areas in the canopy caused by the death of one or more trees (Whitmore, 1989), are the dominant form of disturbance. These gaps not only help maintain the characteristic uneven-aged nature of late successional forests, but also they influence nutrient cycling, preserve soil and plant species diversity, and change the microtopography in many forests. Windthrow gaps have been documented in a variety of ecosystems on every continent. Forest gaps have also been termed nutrient “hot spots” because they tend to be areas with high rates of decomposition and mineralization, leading to increased levels of nutrients (Colines & Pickett, 1988; Poulson & Platt, 1966; Denslow et al. 1998; Ritter, 2005; Scharenbroch & Bockheim, 2007). Thus, gaps play an important role in the overall biogeochemistry of forest systems. Over the last 30 years, numerous studies have been conducted describing gap dynamics (Denslow, 1987; Kuuluvainen et al. 1998; Yamamoto, 1992; Yamamoto, 2000; McCarthy, 2001; Delfan-Abazari et al. 2004; Sagheb-Talebi et al. 2005; Sefidi et al. 2011).  These studies focus on gap impacts on forest structure, nutrient cycling, microclimate, regeneration, restoration and forest management. Although there is extensive literature on gap dynamics, it is often hard for managers to interpret results due to inconsistent methods. In shaded understorey of forests, many suppressed seedlings and saplings wait for many years for the appearance of a canopy gap (Hubbell & Foster, 1996; Forget, 1997; Ashton, 1998; Van Der Meer et al. 1998; Abe et al. 1995). Therefore, forest regeneration processes frequently depend on the natural disturbance regimes (Whitmore, 1989). In fact, canopy disturbances have a major influence in forest communities’ structure and organization, since gaps formed by disturbances will influence the germination, growth and survival of tree seedlings. The response of trees to disturbance depends on the type of species regeneration and on gap features including (dimension, age, morphology, mode and frequency of formation) (Abe et al. 1995; Van Der Meer et al. 1998; Yamamoto & Nishimura, 1999; Imai et al. 2006). Importance of gap dynamics in forest ecosystems was discovered in the early 20th century, and intensive investigation of gap dynamic features are dates back to the late 1970s (McCarthy, 2001). Gap formation changes the amount of total incident light reaching the ground level and influences nutrient and moisture availability (Denslow & Spies, 1990; McCarthy, 2001; Ritter, 2005; Mihok et al. 2005; Galhidy et al. 2005), providing potential establishment sites for regeneration. As the gap dynamic is recognized as a crucial process in forest stand development, it has received much attention during the last several decades (Denslow, 1980; Runkle, 1982; Runkle & Yetter, 1987; White & Pickett, 1985; Brokaw & Scheiner, 1989; Spies & Franklin, 1989; Attiwil, 1994; Seymour et al. 2002). Gap dynamics have been described in tropical (Van Der Meer & Bongres, 1998; Carvalho et al. 2000; Imai et al. 2006), temperate (Abe et al. 1995; Yamamoto, 1995; Coates, 2000; Choi et al. 2001; Ott & Juday, 2002; Gagon et al, 2004; Amanzadeh et al. 2004; Delfan-Abazari et al. 2004; Sagheb-Talebi et al. 2005; Arietta & Suarez. 2005; Naaf & Walf, 2007; Shabani et al. 2011; Sefidi et al. 2011) and boreal forests (Kneeshaw & Bergeron, 1998; Drobyshev, 2001; McCarthy, 2001, Table 1), and being considered a process capable of shaping the structure of plant communities, it expands environmental heterogeneity, in space and time, develops a diversity of establishment and growth chances for tree species. Differences in species shade tolerance levels may determine the ability of immature individuals to grow and survive in gaps of different sizes (Carvalho et al. 2000; Meyer et al. 2000; Schumann et al. 2003; Imai et al. 2006). Gap size is an important characteristic in natural forests and it can strongly influence vegetation growth and nutrient cycling (Zhang & Zak, 1995; Gary et al. 2002; Muscolo et al. 2007). In many studies gaps ranging from 10 to about 2500m2 have been reported (Table 1). Small gaps are originally defined to describe small openings in the forest and are created by the death of branches or one or more trees (Watt, 1947). Large gaps (>1000m2), created through fires, tornadoes, downdrafts, or hurricanes, have characteristics sufficiently different from small gaps which makes it difficult to compare them (Schliemann & Bockheim, 2011) or are created by domino effect by falling of big trees over other trees. In particular, very large openings have reduced shading from surrounding trees and consequently have higher solar radiation and soil temperature than small openings (Zhang & Zak, 1995; Gary et al. 2002; Muscolo et al. 2007) In this study, we have examined stand structural and gap characteristics of tree species in old-growth oriental beech stands of the Hyrcanian forests, north of Iran. Specific objectives were i) to examine stand structure , ii) to examine trends in gap characteristics (gap area, gap size, gap density, gapmaker traits, and number of gap makers), iii) conditions and state regeneration within canopy gaps in the permanent plot in size of 16ha. 

MATERIALS AND METHODS

This study is carried out in the 79 ha natural unlogged oriental beech (Fagus orientalis) stand in compartment 32, district 1, located at Shast Kalateh Forest in the eastern Caspian region, North of Iran on 36° 43′ 27″ N, 54° 24′ 57″ E. A general view and location of the study area is given in Fig. 1. Elevation of the study area varies from 820 to 960m a.s.l., with an average monthly temperature of 15.4°C, with maximum and minimum temperature in July (28.7°C) and in February (8.71°C), respectively. Mean annual precipitation is 650mm. According to the De Martonne and Emberger classifications, the climate of the study area is cold and wet, having a temperate summer with short dry season. Stand total height is about 30 m and the canopy cover varies between 60 and 100 percent (Habashi et al. 2007). 

Soil texture is loam to clay-loam with a pH of 5.5 and soil is classified as a forest brown soil. Mean stand density and standing volume are 235ha-1 and 463m3ha-1, respectively (FRW, 1995 & 2008). The compartment consists of a natural, mixed, uneven-aged deciduous old-growth forest dominated by shade-tolerant Oriental beech with minor components of other broad-leaved species including hornbeam (Carpinus betulus L.), velvet and cappadocian maple (Acer velutinum Boiss. and Acer cappadocicum), Caucasian alder (Alnus subcordata), ironwood (Parrotia persica), date plum (Diospyrus lotus) and elm (Ulmus glabra Huds.). The compartment experienced very limited human intervention and disturbance and had no silvicultural activity in the last 50 years since forest management plans started in Iran. Therefore, this stand could be regarded as an example of an intact and unmanaged natural forest.

 

FIELD MEASUREMENTS AND DATA ANALYSIS

The total surface of compartment 32 is 79ha and we selected 16ha (400×400m) as a permanent research plot in summer 2011. The location of the plot was selected to satisfy the following conditions: i) the permanent research plot should be placed in the natural oriental beech stand without human influence, and ii) the permanent plot should be homogenous regarding the slope and aspect. Then, the permanent plot was divided into 64 subplots (50×50m), where all individuals of natural regeneration and understory trees of DBH ≥ 7.5cm were counted within subplots (Delfan-Abazari et al. 2004; Sagheb-Talebi et al, 2005; Habashi et al. 2007). Moreover, on the entire permanent research plot, all living trees with diameter at breast height (DBH) ≥ 7.5cm, standing deadwood (snags) and fallen deadwood (logs) were measured (Lertzman, 1992; Habashi et al. 2007). The threshold values for snags was the DBH ≥7.5cm and the height > 1.30 m and for logs the small-end diameter ≥ 7.5 cm and length more than 1.30 m. For the living stems and snags the tree species, DBH and only for snags also the height was measured. Tree species, DBH, small- and large-end diameter, total length and the exact location on the sample plot were identified for the logs. On the 16ha permanent research plot, we recorded type of canopy openings—canopy gaps (Runkle, 1982). Canopy gap was the area directly under the canopy opening with the border defined by the crown projections of trees surrounding this canopy opening. When trees within the gap reached the base of canopy of the surrounding forest, a gap was considered closed and not sampled.

Canopy gap was defined as an opening in the canopy with the size at least 40 m 2 that was formed by the mortality of one or more trees from the upper tree layer (with DBH ≤ 20 cm), and where the standing or lying remnants of the gap maker were detectable. For each canopy gap, two parameters were measured—the length (L) as the longest distance within the gap and the width (W) as the largest distance perpendicular to the length. Gap form was considered as ellipse and the area of canopy gap was calculated using the formula for an ellipse: A=πLW⁄4, Gapmaker was considered to be a tree from the upper tree layer whose death caused an opening in the canopy. On the other hand, Gap makers were characterized with the following descriptors: type (snapped, root-thrown, dead standing, and leaning), species, and diameter at breast height.

The number of gap makers for each gap was recorded, and the tree species and the DBH were identified for each gapmarker as well.

Regeneration (gap filler) was sampled within all gaps with seedling (et al. 2004).

In all gaps “definitive gap fillers” were measured (Sefidi et al. 2011).  Additionally, we selected the gap filler most likely to replace each gap maker. These definitive gap fillers were chosen based upon their height, location, and a visual assessment of their overall condition (Lertzman, 1992). In most cases, we could easily designate the definitive gap fillers because they were considerably taller than other gap fillers, and they often showed a height growth release in response to gap formation that was easily seen in the field, especially for beech and hornbeam. Most definitive gap fillers in this study were pole-sized trees with DBH 7.5-12.5 cm and 8-15 m tall.

 

 

Table 1. Comparison of forest stand and canopy gaps characteristics in differences studies

Location

Forest cover type (species)

Forest age (year)

Canopy gap size a

(m2 )

References

Germany

Fagus sylvatica

Old growth

116–1410

Naaf and Wulf (2007)

Japan

Fagus crenata

–b

<100–1200

Henbo et al (2004)

Chile

Nothofagus pumilio

Old growth

50–500

Fajardo and de Graaf

(2004)

Slovakia (Western Carpathians)

Fagus sylvatica (beech– dominant)

Old growth

Canopy gap 5-568

Expanded gap

66-1367

Kucbel et al (2010)

Iran,Asalem

Fagus orientalis

Multi age

89-2279

Amanzadeh et al (2004)

Iran, Kelardasht,

Fagus orientalis

Multi age

25-1098 (550)

Delfan-Abazari et al (2007)

Iran

Fagus orientalis

Multi age

34- 597 (210)a

Mataji et al (2008)

Iran, Lalis

Fagus orientalis (mixed beech stand)

Multi age

600

Shabani et al (2010)

Iran,

kheyrud-kenar

Fagus orientalis (mixed beech stand)

Old growth

19.6-1250 (178)

Sefidi et al (2011)

Iran, Gorgan

Mixed beech stand

Old growth

48.6-622.5 (147.5)

This work

 

 

Fig.1 Location of the study site in the Hyrcanian Forest

 

 

RESULTS

Stand structure and composition

The mean density and volume of the studied permanent research plot were 287 Nha-1 and 472 m 3ha-1, respectively. Dominant tree species was beech with a proportion of 40% in stem number and which was only counted for 55.8 % of standing volume. The proportion of stem number per ha for hornbeam and ironwood was 21.2% and 26.9%, respectively. While the volume proportion of these two species was 24.1% and 10.4%, respectively. Other species were counted to 11.5% of stem number and 9.7% of stand volume (Table 2). Although the other species present in the stand reached a relatively high number (11.6%), they accounted for only 9.5 % of volume.  Of total deadwood, standing deadwood accounted 32.6% and fallen deadwood consisted of 67.4 % within the canopy gaps (table2). Total amount of deadwood was 27.75 Nha-1 and 45.4 m 3 ha-1, which was counted to 8.7% of total density and 9.1% of total volume of living trees. The deadwood proportion of beech, hornbeam, ironwood and other species logs was 31.4, 32, 21 and 15.6%, respectively. The volume proportion of these three species was counted to 62.5, 25.51, 8.62 and 4%, respectively (Table 2). 

 

GAP CHARACTERISTICS

Overall, 54 canopy gaps were identified on the permanent research plot with a total area of 7966.5 m2 (Table3) that covers 4.98% of the total area. Minimum, maximum and mean gap size

 

was 48.3, 622 and 147.5 m2. Half of the gaps were smaller than 100 m2, covering 2051.1 m2, which counted for 25.7% of the total gap area. The other half of the gaps were larger than 150 m2; among them only one gap was larger than 600 m2. Gaps showed different directions, mostly north, south-west and north-west directions counting for 33.3% north, 25.9% south-west and 16.7% north-west of the whole gaps. The highest mean gap size (ca.140 m2) was found on east and west directions (Table3).  Density of gap makers was 7.6 Nha-1, and mean, minimum and maximum DBH of them were 63.16 cm, 21.7 cm and 115 cm, respectively. Of total deadwood, standing deadwood counted to 32.6% and fallen deadwood consisted of 67.4% within the canopy gaps (Table3). Range of gaps varied within gap size, that 27 numbers (50%) were in the gap class 100 m2 and other species 50% were in the other gap classes. Only one gap (1.85 %) of total gaps recorded in the gap class was greater than 600 m2. The largest gap area belonged to gap classes lower than 100 m2 with 2051 m2 and the smallest included gap class above 600 m2 with (622 m2). The most frequent were the canopy gaps with the size from 48.5 to 150 m2, i.e. gap classes 2 and 150 m2 (68.5%). Whereas more than 70% of these categories were consisted by the gaps 2.  About seventy-eight percent of the gaps was less than 200 m2 in area and only 7% of the gaps exceeded 500 m2 (Table 4) gaps larger than 300 m2 composing 14.7 % of total gaps frequency, but they formed 35.1% of the total area covered by gaps. The mean frequency direction of tree falls and gaps were in accordance with the prevailing winds, e.g. North (0°) and southwest (240°) (overall 58% of total gaps) in the surveyed area (Table 5). Fig. 2 shows the distribution of the total gap area according to the size categories of canopy gaps. While the small gaps (2) made up nearly 50 % of gap maker, their proportion of the total gap area reached only 25.7%. On the other hand, one largest recorded gap made up to 7.8% of the overall gap area. The most frequency of the gaps size 2 comprised about two-thirds of gap area, whereas the largest gap made up an over proportion amount of 9.6%.

 

GAP MAKER CHARACTERISTICS

A total of 95 gap makers were identified within the 54 studied gaps, making an average of 7.6 Nha-1.

More than third-quarter of the gaps were made by one or two gap makers, 50% by one and 31.5% by two gap maker; there was only one gap that was made by 7 gap makers (Fig. 2). The area of gaps made by one gap maker varied between 48 m2 and 252 m2, while that of made by 7 gap makers was 622 m2 (Table 5). Beech was the most common gap maker (52%) followed by hornbeam (26.6%), ironwood (16%). Velvet maple, Caucasian alder and date plum were other gap makers with total proportion of 5.4 %. The minimum, maximum and mean DBH of the gap makers was 21.7, 63.2 and 115 cm, respectively.

The mean DBH of beech was the highest (70.6 cm) among the gap makers, whereas that of date plum (21 cm) was the lowest (Table 6).

The most common cause of canopy gaps was a single tree-fall and two tree-fall events with (52 and 34%). While gaps caused by three and more trees were very little (14%). The maximum number of fallen trees within a single gap opening was 7.  Fig. 7 showed that beech had the highest percent of gap maker among species (52%) and Caucasian maple had the lowest (2.4%). While this species had the highest frequency gap-filler among species (29%).  As the tress creating gaps were identified using woody debris analysis, a two-trees gap might be identified in which the first tree died 40 years ago and the second tree one year ago. Regarding the land area of gap size classes, a distinctive disproportion between the gap frequency and gap area was observed.

 

GAP REGENERATION

A total of 37167.4 seedling and sapling per hectare were measured in the 54 gaps studied (Table7). Velvet maple (28.8%) and beech (24.1%) had the maximum frequency among regeneration. Ironwood (15.4%), hornbeam (14.8%) and date plum (11.5%) were the next important contributors to the regeneration pool. Approximately, 84% of the total regeneration, namely the seedlings was shorter than 1.30 m in height class (Table 7).

The proportion of saplings with DBH less than 2.5cm was 11%, saplings with DBH 2.5-7.5 cm were 4% and saplings with DBH 7.5-12.5 cm were 1%. The frequency of regeneration of different species in different gap sizes is given in Fig. 4. With increasing gap size, the number of beech regeneration decreases, while that of hornbeam and velvet maple increases.

 

 

 

Fig. 2. Proportion of gaps made by gap makers.

 

 

 

 

 

 

 

 

 

Fig. 3. Frequency of gap makers and gap filler species in the 54 gap studied.

Table 2. Main characteristics of the living trees and deadwood on the studied permanent research plot

Tree species

 

Density ha-1

 

Volume ha-1

N

%

 

V

%

Living trees (DBH ≥ 7.5)

Beech

115

40

 

263.4

55.80

Hornbeam

61

21.2

 

113.8

24.1

Persian ironwood

77

26.9

 

49.0

10.4

Other species*

33

11.5

 

45.80

9.70

Total

287

100

 

472

100

Standing deadwood (snags)

Beech

2.6

24.8

 

5.1

56.7

Hornbeam

2.8

26.7

 

1.4

15.6

Persian ironwood

2.6

24.8

 

1.3

14.4

Other species

2.5

23.7

 

1.2

13.3

Total

10.5

100

 

9.0

100

Fallen deadwood (logs)

Beech

5.4

31.4

 

22.7

62.5

Hornbeam

5.5

32

 

9.1

25.1

ironwood

3.6

21

 

3.1

8.62

Other species

2.7

15.6

 

1.47

4

Total

17.2

100

 

36.4

100

 

Table 3. Characteristics of the studied gaps in the permanent research plot

Canopy gap size m2

 

number

%

 

Total area (m2)

%

<100

 

27

50

 

2051.1

25.74

150

 

10

18.5

 

1320.4

16.6

200

 

5

9.25

 

869

10.9

250

 

4

7.4

 

910

11.4

300

 

3

5.5

 

773.8

9.6

350

 

2

3.7

 

649.4

8.1

400

 

2

3.7

 

770.5

9.6

>600

 

1

1.8

 

622.4

7.8

Total

 

54

100

 

7966.50

100

 

 

Table 4. Characteristics of gaps in relationship with geographical direction

Geographical gap direction

No of gap

%

Mean  gap size (m2)

%

N

18

33.3

131

14.2

NW

9

16.7

120.5

13.10

W

5

9.2

140

15.2

SW

14

25.9

119

12.9

S

4

7.40

97

10.5

SE

1

1.8

94

10.2

E

2

3.7

143

15.5

NE

1

1.8

75

8.1

Total

54

100

147.5

100

 

 

 

Table5. Characteristics of the studied gaps in relation to number of gap makers

number of gap maker

number of gaps

Canopy gap size (m²)*

Total area (m2)

1

29

91.5 (48-252)

2655.5

2

17

166 (74.5-393)

2818.9

3

3

193 (154-234)

574

4

4

324 (269-378)

1296

5

0

0

0

6

0

0

0

 

7

1

623

623

 

Total

54

201.5

7966.5

 

 

 

 

 

 

 

 

* Numbers within parenthesis are minimum and maximum gap size

Table6. Characteristics of the studied gaps based on gap maker species

Species

number of gap

%

Mean DBH (cm)

mean area of gap (m²)

Beech

39

52

70.6

160.5

Hornbeam

20

26.7

66

170.2

Ironwood

12

16

45.3

103.8

Velvet  maple

2

2. 7

45.7

327.6

Caucasian alder

1

1.3

57.5

223.5

Date plum

1

1.3

21.0

236

 

 

 

 

 

 

 

Table7. Number and frequency of seedlings and saplings (Nha-1) by species in the canopy gaps on the permanent research plot

 

Height class (m)

 

Diameter classes (cm)

Species

≤1.30

%

 

0-2.5

%

 

2.5-7.5

%

 

7.5-12.5

%

 

Total

%

Beech

7496.1

23.8

 

831.2

20.2

 

466.9

36.7

 

150.4

45.6

 

8944.7

24.1

Hornbeam

5058.8

16.1

 

348.7

8.4

 

105.7

8.3

 

20.7

6.3

 

5534

14.8

Ironwood

4268.1

13.5

 

1060.2

25.6

 

345.2

27.2

 

66.3

20.1

 

5739.8

15.4

Velvet maple

9821.4

31.2

 

809.3

19.6

 

75.2

5.9

 

9.5

2.9

 

10715

28.8

Date plume

3339.5

10.6

 

629

15.2

 

224

17.6

 

82.6

25

 

4275.2

11.5

Cappadocia maple

1450.8

4.6

 

113.7

2.7

 

52.8

4.2

 

0

0

 

1617.4

4.35

Lime

0

0

 

132.6

3.2

 

0

0

 

0

0

 

132.62

0.35

Elm

0

0

 

208.2

5

 

0

0

 

0

0

 

208.15

0.56

Total

31414.8

100

 

4133

100

 

1269.9

100

 

329.9

100

 

37167.4

100

%

84

 

 

11

 

 

4

 

 

1

 

 

100

 

 

 

 

Fig 4. Proportion of regeneration of different species in different gap sizes

 

 

DISCUSSION

Ecosystems are a product of the interactions of biota, climate, edaphic conditions, and disturbance processes. Over long periods, species best suited to the prevailing conditions eventually succeed and dominate (Denslow, 1980). This study in the Shastkalateh Forest, Hyrcanian region revealed the characteristics of canopy gaps in a natural unlogged oriental beech forest. The results of this study showed that density and volume were 287 Nha-1 and 471 m3.ha-1, respectively. Beech had the highest proportion volume of living trees (55.8%) and deadwood (62%) among other species (Table2). It can be concluded that the structure of studied natural unlogged oriental beech forests in the Hyrcanian region is old growth, irregular and uneven- aged. Previous investigations in Hyrcanian Forests confirm this findings, too (Falah, 2000; Sagheb-Talebi & Schütz, 2002; Sagheb-Talebi et al. 2005; Habashi et al. 2007). Results showed that canopy gap size varied between 48.5 m2 and 623 m2. Total canopy gaps area was 7966 m2 that nearly covered 5% of the permanent research plot. Sefidi et al (2011) found that canopy gaps covered 9.3% of the total forested area in the mature Fagus orientalis-dominated stands of northern Iran. This amount is less than the value obtained in the study of Sefidi et al (2011), but close to the 4% of total forest area in the unmanaged stand in natural beech forest in the Keyrodkenar, Noushar (mataji et al. 2008) and 4.7% identified for mature Picea-Fagus forests in the Appalachian Mountains the of eastern United States (Rentch et al. 2010). Although, canopy gap fraction generally decreases with stand age (Hart & Grissino-Mayer, 2009), management can also influence gap fraction (Sefidi et al. 2011). Also, Zeibig et al (2005), found a 5.6 % gap proportion and 137m2 average gap sizes in Krokar (Slovenia). The size of gaps is obviously closely linked to the number of trees involved in its creation. We found that most gaps were formed from single and then two tree- fall events and identified no gaps formed by 5 and 6 gap makers. But we found only one gap formed by 7 gap makers.  In contrast (Sagheb-

 

Talebi et al. 2005), in the Mazandaran forests of northern Iran, found gaps that were formed from up to six treefall events while Delfan-Abazari et al (2004), in the Kelardasht forests, of northern Iran, found most gaps were created during double-tree fall events. Sefidi et al (2011), who worked at the Kheyrudkenar Experimental Forest, found one characteristic of canopy gaps that differed from the others. They determined that the most canopy gaps are formed by one tree-fall and there was not any gap that formed by more than 4 gap makers. Although our site represents a mature beech forest, the trees are growing on well-drained, deep soils which may reduce the likelihood of a single tree-fall event cascading into multiple trees.

The results of this study showed that 86% of the gaps area fluctuated between of 50 and 200 m2.  In constant Delfan-Abazari et al (2004) in the Kelardasht Forest found that the area of most of the gaps varied from 300 to 500 m2, but the results of study conducted by Sefidi et al (2011) were similar to these of the present study.  Also other studies suggest different gap area ranges from 80 to 1230 m2 in the Golband Forest, 89 to 2279 m2 in the Asalem Forest (Amanzadeh et al. 2004), 63 to 1383 m2 in the Mazandaran beech Forest (Sagheb-Talebi et al. 2005) and 34 to 579 m2 in the Kheyroudkenar, Noushar (Mataji et al. 2008). Researches in Iranian beech forests identified that most gaps are formed as a result of single tree-fall (Sefidi et al. 2011) and two tree-fall event (Delfan-Abazari et al. 2004; Sagheb-Talebi et al. 2005).

Nevertheless, we found that substantial majority of gaps were formed by single tree-fall event. Usually beech has higher frequency than other species in the small gaps (Shabani et al. 2011). Research in forests in Slovenia showed that Acer requires large gaps to successfully reach the overstory, but Fagus sylvatica was able to reach the canopy in all gap sizes and was particularly successful in capturing gaps that were 2 (Najel et al. 2010). The same patterns may exist in the Iranian forests and would explain the presence of beech and Velvet maple seedlings in all gaps, but the dominance of beech as gapmaker. The growing conditions for the young seedlings and sapling within a gap are also depending upon gap size. Seedlings and saplings growing in the smaller gaps found in beech forests will experience lower cover from competing herbaceous cover and faster litter decomposition rates (Galhidy et al. 2006). The results of this study showed that the frequency regeneration of beech and ironwood regeneration decreased with increasing gaps size. In contrast, frequency Velvet maple, hornbeam and other species (including date plum and Cappadocia maple) enhanced. One reason is that the beech is a shade tolerant species and with expanded gap area the environment conditions for its regeneration decreases. Because, more light reaches the surface of canopy gap. While maple, date plum and even hornbeam are light demanding species that have more frequency than shade tolerant species within large gaps. While studying forest dynamics, in-depth knowledge on regeneration has both theoretical and practical importance. Our findings in this study indicated that an average of regeneration a total of species was 37147Nha-1. Velvet maple and beech had more than half of regeneration amount in the canopy gaps allocated. Other studies in the Hyrcanian Forests reported the number of seedlings and saplings of all species between 10300 and 17600 (Delfan-Abazari et al. 2004) and 30 thousand to 120 thousand Nha-1 (Amanzadeh et al. 2004). The amount of regeneration in our study in Golestan province was higher than in Kelardasht Forest in Mazandaran province (Delfan-Abazari et al. 2004) and Kheyrud Forest with 3398 Nha-1 (Sefidi et al. 2011)

Kenderes et al (2008), found that average seedling density in the studied natural gap was between (between 40000 and 50000 per hectare) that is regarded as sufficient for restocking managed beech stands by natural regeneration. research in the Caspian region demonstrated that, although oriental beech regeneration had the best growth characteristics within gaps larger than 1000 m2, more well-formed and healthy saplings were found within gaps of 200–500 m2 (Sagheb-Talebi & Shütz, 2002). Tabari et al (2005), concluded that small gaps provide a higher stability and more favorable environmental conditions for survival and growth of beech seedlings.  Also, lack of sufficient seedlings within the openings of the beech forests of Iran is due to regeneration deficiency, weed competition and seed production deficiency. Therefore, where advanced regeneration of beech is present, all chances for further development should be given by gradually opening the canopy layer. Also, according to Hungarian forestry regulations, the presence of at least 10000 individuals per hectare is required for regeneration to be accepted as successful. Mihók et al. (2005) and Gálhidy et al. (2006) for Hungarian beech forests confirmed the effects of gap size on regeneration success. Studies of Korpel (1995), showed that the regeneration in European virgin beech forests occurs in small groups with a surface of 100 to 200 m2, and openings of over 2000 m2, which could be covered by regeneration in the late decay stage, are a seldom .

Our study focuses on gap regeneration patterns in a natural untouched beech forest stand. Although we only showed a snapshot of a dynamic process, we tried to interpret the findings as an outcome of several important dynamic processes: gap existence, tree regeneration, gap maker characteristics, geographical direction gap and coexistence of other species. Our findings emphasize the importance of the spatial scale of disturbances, and of the gradual change in abiotic factors (e.g. light) from below canopy to gap center in gap-studies. Gap regeneration patterns depend not only on the ecological traits of tree species (e.g. light demanding, shade-tolerant etc.), but also among others, on the composition and cover of herbaceous vegetation and on game browsing. Therefore, gap studies should focus on these factors as well, in order to get a better understanding of regeneration mechanisms of forest stands. In situations where forest managers are attempting to increase the establishment of beech in managed stands through the creation of gap, Sefidi et al (2011), indicate that there is no relationship between canopy gap size and density of beech seedlings.  However, it is important to differentiate between seedling germination (characterized by the seedling density that we measured) and seedling establishment. Results Kenderes et al (2008), study also indicated that natural regeneration was possible in naturally occurring gaps. Both the density and species composition of regeneration would enable the development and long-term maintenance of mixed beech-dominated forests. In conclusion, we argue that in spite of the limitations set by their small size and the negative effects from the surroundings (e.g. longevity, diseases, and wind), forest reserves are useful tools of studying natural processes in the Hyrcanain Forest.

Taking into account the stand structure and light regime in small and medium-sized gaps, the potential for the application of the group selection system in Caspian beech forests has recently been investigated (Sagheb-Talebi & Schütz, 2002), where the removal of two to four main trees is proposed. It should be noted that beech and Velvet maple were the most common gap filler even though the main gap makers were beech, hornbeam and Velvet maple. This suggests that a shift in species composition is occurring, though slowly. Because beech species is shade tolerant, single-tree selection would provide great flexibility in controlling residual stocking, tree quality, and establishing a cutting cycle that meets both ecological and economic objectives. More intensive measures, such as understory herbiciding and planting, may be needed for those forests lacking adequate beech regeneration. However, given the paucity of experimental evidence and potentially changing environmental conditions, we believe our study provides a foundation that forest managers could use to develop adaptive forest management techniques for restoration objectives. Canopy gaps are the dominant source for regeneration in mature beech forests in northern Iran (Sefidi et al. 2011). Most gaps form single-tree fall events and the deep soils in this region may prevent the cascading effect of surrounding trees following the initial tree fall. Thus, most gaps tend to be small (medium gap size was 178 m2) and small gaps were irregular in shape. Across the range in gap sizes that we measured (19.6–2246 m2) there was no relationship between gap size and seedling density for either of the dominant species in this stand (F. orientalis and A. velutinum). Oriental beech was clearly superior at capturing canopy gaps compared to other species and was identified as the definitive gap filler in 93% of the gaps. A weak point of the present study is the fact that no gap sizes between 200 and 600 m2 were studied. Although we clearly found different seedling responses between small (50 and 200 m2) and large gaps (600 m2 and more), it was not possible to determine the “critical gap size” exactly, at least if there is one. Another weakness is the relatively short monitoring period. Similar researches can therefore be recommended over longer time periods in such gap sizes and also in gaps of 200–600 m2 (with several replicates) of various beech stands, with different exposition, inclination and altitude. The findings of our study can be used for the development of techniques and treatments for close to nature silviculture in the beech stand forest. The observed gap dimensions and other characteristics of canopy gaps can guide Forest managers and researchers towards practices that ensure continuous forest cover.

 

ACKNOWLEDGEMENTS

The authors gratefully acknowledge the assistance of Mr. M.Nasrabadi, J. Mohamadi and A. Amiri for data collection. This work was conducted while Mojtaba Amiri was a Ph.D. candidate of Forest Sciences.  Also, financial support was provided by the Gorgan University of Agricultural Sciences and Natural Resources.  

 

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