Gap formation and susceptible Abies trees to windthrow in the forests of Odaesan National Park
Gap formation and susceptible Abies trees to windthrow in the forests of Odaesan National Park
Journal of Ecology and Environment. 2015. May, 38(2): 175-183
Copyright © 2015, The Ecological Society of Korea
This is an Open Access article distributed under the terms of the Creative Commons Attribution Non-Commercial Licens ( which permits unrestricted non-commercial use, distribution, and reproduction in any medium, provided the original work is properly cited.
  • Received : March 18, 2015
  • Accepted : March 27, 2015
  • Published : May 28, 2015
Export by style
Cited by
About the Authors
Mina, Jeon
Department of Biological Sciences, Kangwon National University, Chuncheon 200-701, Korea
Kyungeun, Lee
National Institute of Ecology, Seocheon 325-813, Korea
Yeonsook, Choung
Department of Biological Sciences, Kangwon National University, Chuncheon 200-701, Korea

Extremely strong winds and heavy rainfall caused canopy gaps in a mixed Abies holophylla broadleaf forest and a Quercus mongolica -dominated forest in Odaesan National Park, Korea in October 2006. The impact of the combination of strong winds and torrential rain on the development of forest gaps and canopy structures were investigated. The mean size of newly created gaps were 205 m 2 in the mixed forest and 86 m 2 in the Quercus forest, and were created by 2.8 and 1.4 gapmaker trees, respectively. Among the 73 trees lost in the mixed forest, 59% succumbed because of direct wind damage while 41% were struck by neighboring trees that fell into them. Most of these trees downed by wind were uprooted (74%), while the trees downed by neighboring tree falls snapped (78%). 21 trees in the Quercus forest died from direct wind damage, and 57% of them were uprooted. Although the relative density of Abies nephrolepis and A. holophylla represented only 0.2% and 6.4%, respectively, of all species in the intact mixed forest, they accounted for 27% and 15%, respectively, of all trees affected by wind on that site. In fact, 85% of the total A. nephrolepis and 91% of the total A. holophylla in the mixed forest fell directly due to strong wind. By contrast, only one Abies species , A. nephrolepis , was found in the Quercus -dominated forest, and it accounted for 7.3% of the species composition. These findings suggest that A. nephrolepis and A. holophylla are particularly susceptible to high winds because of their great heights and shallow root systems.
Disturbance is defined as “any relatively discrete event in time that disrupts ecosystem, community, or population structure and changes resource, substrate availability, or the physical environment” ( White and Pickett 1985 ). Its impact depends upon the type, scale, intensity, and frequency. Two types of disturbances have been identified: 1) largescale, occurring over a wide area and causing great destruction; and 2) small-scale, in which branches or stems are broken and trees either snap or are uprooted ( Kang and Choi 2000 ). Although the frequency of largescale disturbances is generally very low, some events, such as hurricanes or typhoons, can destroy an entire forest ( Lorimer 1977 , Bormann and Likens 1979 , Canham and Loucks 1984 , Boerner and Cho 1987 ). In contrast, small-scale disturbances occur more frequently, and are characterized by falling trees that can create a mosaic of various vegetation types and ages ( Runkle 1982 , Cho 1989 , Cho and Boerner 1991 ).
A forest gap forms in the canopy when individual or multiple trees fall, or when large branches are broken on a single tree ( Cho 1992 ). Strong winds are associated with approximately 97% of all gaps formed in mature forests within the southeastern United States and 80% of all new openings in Costa Rican rain forests ( Barden 1981 , Lawton and Putz 1988 ). Species with shallow root systems are especially vulnerable to high winds ( Ruel et al. 2001 ). When large trees are uprooted, the forest floor is significantly altered because seeds lying within the soil become exposed and germinate, and the physical and chemical nature of the soil is changed by penetrating light ( Greenberg and McNab 1998 ). In addition, soil gaps such as pits and mounds ( Peterson and Pickett 1990 ) may lead to new microsites that can support the development of vegetation, ultimately changing the overall forest structure ( Clinton and Baker 2000 ).
Odaesan National Park in Korea is a mosaic of various mature forests. The largest area is dominated by pure stands of Quercus mongolica . However, mixed forests also exist, including stands of Q. mongolica with broad-leaf species Tilia amurensis , Acer mono , and A. pseudo-sieboldianum , or a combination of deciduous trees with conifers such as Abies holophylla ( Lee et al. 2006 ).
In October of 2006, forests within this park were subjected to strong winds and heavy rainfall. Throughout the eastern coast of Gangwon-do, including Sokcho, Gangneung, Donghae, and Pyeongchang (where Odaesan is situated), this storm inflicted damage to humans, buildings, fishing boats, and roads ( Shin and Park 2006 ). A maximum gust of 63 m/s was measured at Sokcho, along with sustained winds of 31 m/s, and precipitation during this event totaled 232 mm. Throughout that month, Yangyang, Gangneung, and Donghae received record high precipitation, as well as winds in the typhoon category that exceeded 17 m/s. The nearest weather station, 22 km away in Daegwallyeong, indicated gusts of 22.5 m/s and a historically high 171.5 mm of rain during a single day ( Korea Meteorological Administration 2008 ). Although weather conditions were not recorded at Odaesan during this storm, the largest old-growth tree, an A. holophylla (diameter, 171 cm; height, 33 m) was uprooted at the time ( Lee . 2006 ). Damage to other trees also led to the formation of forest gaps.
Fortunately, we have been monitoring several types of forests in the Odaesan National Park since 2005. The information of these reference forests provides a great opportunity to understand the structure and dynamics of the forests at the stand and species level ( Kim 1996 ). Therefore, we investigated how the combination of strong winds and torrential rain, which are typical for Odaesan National Park, affected the development of forest gaps, influenced representative canopy tree species, and finally selected susceptible tree species to windthrow in that location.
- Study sites
Odaesan National Park represents a typical forested area populated by deciduous broadleaf tree species in central Korea. We examined the impact of wind damage on the structure of two types of forests there: 1) a mixture of the conifer A. holophylla and broadleaf species (hereinafter “mixed forest”), and 2) an area dominated by Q. mongolica (hereinafter “ Quercus forest”). The mixed forest is located at Somyeonggol, on the lower slope of Birobong (1563 m), which is the highest peak in the park. This is an area where changes in vegetation structure have been monitored annually since a 2-ha permanent plot was installed in 2005. In the permanent stand of the reference forest, which did not suffer from wind, the tree density was 837 stems/ha with a diameter at breast height (DBH) >5 cm and an average basal area of 28.5 m 2 /ha in 2008 ( Odaesan National Park Service 2008 ). The main tree species included T. amurensis and Acer pseudo-sieboldianum , which had importance values (IVs) of 17% and 16%, respectively. Conifer tree species, A. holophylla in that forest had an IV of 12.4%. The stand age of the forest was approximately 120 years old based on calculations of allometric relations ( Lee et al. 2006 ). The IV (%) is the sum of the relative density (%) and the relative basal area (%) divided by 2.
The Quercus forest is located along the upper slope of Hyoryeongbong (1560 m). A reference stand that had not suffered from the wind was investigated in 2007, and its average density was 1,230 stems/ ha (DBH >5 cm), and the average basal area was 44.2 m 2 /ha. The dominant species was Q. mongolica (IV of 43%), followed by T. amurensis (16.5%) and A. pseudo-sieboldianum (14.2%). Another conifer, Abies nephrolepis (IV of 7.2%), was more common in the Quercus forest than in the mixed forest.
Our research area has a typical continental climate. The average annual temperature at the Daegwallyeong weather station is 6.4°C, and the average monthly temperatures range from –12.5°C (January) to 22.9°C (August). The average annual precipitation is 1,717.2 mm, with most rain falling in the summer ( Korea Meteorological Administration 2008 ).
- Measurement of forest gaps and identification of gap-maker tree species
The total number of forest gaps that formed following the storms on October 23 rd and 24 th of 2006 was determined for the mixed and Quercus forests by using data that was obtained from a survey of stems and leaves from fallen trees in March 2007. The damaged area for the mixed forest was about 15 ha. Although there is no definitive value when describing the size of a forest gap ( Barden 1989 ), we used measurements of the bases of gap-bordering canopy trees for our estimations ( Runkle 1981 ). For border trees, the criterion was based on trees in the canopy layer. If the height of a mid-layer tree was more than two-thirds of the average for canopy trees, it was considered to be part of the border. Gap sizes were measured by positioning the base of bordering trees via a GPSMAP 60CS (Garmin Ltd., Olathe, KS, USA).
Gap-maker trees (DBH of ≥5 cm) were defined as those that contributed to the creation of gaps because they had either been uprooted or broken directly by the wind, or were struck by neighboring trees that had fell. The species of windthrown trees were identified, their DBHs were measured with the direction in which they fell, and they were labeled as either uprooted or snapped. The elevation, aspect, and slope of each gap were determined with an altimeter, compass, and clinometer, respectively. The soil depth at each site was measured by poking a 5-mm-diameter steel pipe into the ground six times.
- Formation of forest gaps
The topographical characteristics of the canopy gaps in the two forest types are shown in Table 1 . A total of 26 gaps were confirmed in the mixed forest. They appeared on the steep northeast-facing slope (average 37°) at an elevation of 990 to 1160 m, where the soil was very shallow, i.e., 13.8 cm. Because that area was a scree, it was difficult to determine the depth to which the trees had rooted. In contrast, the Quercus forest had 15 gaps, which were located at 1225 to 1405 m, elevations that were higher than for the mixed forest. In the Quercus forest, 86% of the trees grew on the northeast-facing slope (average 30°). Although damage in the mixed forest occurred mostly on the northeast slopes, 46 trees (56%) that were downed in the windstorm fell toward the southeast ( Fig. 1 ). For the Quercus forest, 90% of the 21 damaged trees fell either southeast or southwest ( Fig. 1 ).
Topographical characteristics associated with canopy gaps formed in two forest types
PPT Slide
Lager Image
1average ± standard deviation with ranges in parentheses 2not determined n, number of canopy gaps.
PPT Slide
Lager Image
Distribution of DBH and tree-fall direction for gap-maker trees. (a) mixed forest; (b) Quercus forest. DBH, diameter at breast height.
The 26 gaps in the mixed forest covered an average area of 205 m 2 (75-442 m 2 ), with 73% of them being 100 to 300 m 2 in size ( Fig. 2a ). In contrast, the 15 gaps in the Quercus forest averaged 86 m 2 (23-217 m 2 ), with most being smaller than 100 m 2 ( Fig. 2b ).
PPT Slide
Lager Image
Size of canopy gaps (a and b) and number of downed trees that created individual gaps (c and d). (a) and (c) mixed forest; (b) and (d) Quercus forest.
A gap develops when a tree or trees in the upper canopy fall. Here, the average number of gap-maker trees was 2.8 and 1.4 in the mixed forest and Quercus forest ( Fig. 2c and Fig. 2d ), respectively. Approximately 69% of the gaps in the mixed forest was formed when two or three trees fell ( Fig. 2c ), while 87% of the gaps in the Quercus forest resulted from a single tree-fall ( Fig. 2d ). In the mixed forest, some gaps were formed after the collapse of six tree makers. This we attributed to the fact that broadleaf trees with multiple stems, such as the T. amurensis , collapsed simultaneously.
- Characteristics of gap-maker species
The 26 gaps in the mixed forest resulted from the fall of 73 trees. Among these, 46 (63%) were downed by wind, while the remaining 27 were struck by neighboring trees as they fell ( Table 2 ). The average diameter of trees directly damaged by wind was 41.5 cm compared with 25.4 cm for those that were indirectly damaged by falling trees. Most of the windthrown trees (73.9%) had thick trunks and, thus were uprooted, while those hit by neighboring trees (67.8%) had narrower trunks and, instead, were primarily snapped ( Fig. 3 ). The 15 gaps in the Quercus forest were produced in response to the loss of 21 trees, all of which had fallen directly due to the wind (12 were uprooted and 9 snapped) ( Table 2 ). The average diameter of those damaged trees was 30.4 cm.
Causes of tree-fall and death of trees in two forest types
PPT Slide
Lager Image
1average ± standard deviation DBH, diameter at breast height.
PPT Slide
Lager Image
DBH distribution of gap-maker trees that either fell in direct response to wind or were struck by neighboring tree. (a) mixed forest; (b) Quercus forest. DBH, diameter at breast height.
In the mixed forest, the gap-maker trees were members of 18 species. The largest proportion (27.3%) was the Abies nephrolepis with 20 trees, followed by A. holophylla (11 trees, or 15.1%) ( Fig. 4a ). These two species accounted for 85.0% to 90.9% of the tree-falls directly related to wind, and their frequencies were much higher than any other species in that forest type. Only one species, A. nephrolepis , was a gap maker in the Quercus forest, and all fell directly due to the wind ( Fig. 4b ). Trees of that species also had the largest basal area of 2.9 m 2 , followed by A. holophylla’s basal area of 2.4 m 2 . Although the number of A. nephrolepis trees was similar in both the Quercus and the mixed forests, their average basal area was only 1.6 m 2 in the mixed stand.
PPT Slide
Lager Image
Species-specific causes of death based on number of gap-maker trees (a, b) and type of damage (c, d). (a) and (c) mixed forest; (b) and (d) Quercus forest. Abi nep, Abies nephrolepis; Abi hol, Abies holophylla; Ace mon, Acer mono; Ace pse, Acer pseudo-sieboldianum Ace teg, Acer tegmentosum; Bet sch, Betula schmidtii; Car cor, Carpinus cordata Cor con, Cornus controversa; Pin kor, Pinus koraiensis; Que mon, Quercus mongolica; Til amu, Tilia amurensis.
Of the gap-maker trees in the mixed forest, 60% of A. nephrolepis and 82% of A. holophylla were uprooted, indicating their susceptibility to such damage ( Fig. 4c ). Even though T. amurensis is a deep-rooted deciduous species, many of them were either directly damaged by wind or uprooted. This was due to their clumping habit, in which multiple stems develop when trees re-sprout following a disturbance. The proportion of A. nephrolepis trees that were uprooted by wind (57%) was similar between the Quercus forest and the mixed forest ( Fig. 4d ).
To investigate whether particular tree species are more vulnerable to wind damage, we compared species composition between our designated windthrown forests and nearby undamaged reference plots. The relative density of A. pseudo-sieboldianum was very high at the reference sites for the mixed forest, followed by T. amurensis ( Table 3 ). In contrast, the relative density for the gap-makers A. nephrolepis and A. holophylla was 39% and 23%, respectively, which was different from their calculated 0.2% and 6.4%, respectively, in the reference forest.
Species composition of gap-maker trees directly damaged by wind in mixed forest compared with population in nearby undisturbed reference forest (DBH ≥5 cm)
PPT Slide
Lager Image
DBH, diameter at breast height.
In the reference plots for the Quercus forest, Q. mongolica dominated, followed by A. pseudo-sieboldianum and T. amurensis . Although A. nephrolepis accounted for just 7.3% of the total, only trees of that species were damaged, leading to the formation of gaps in the damaged Quercus forest ( Table 4 ).
Species composition of gap-maker trees directly damaged by wind inQuercusforest compared with population in nearby undisturbed reference forest (DBH ≥5 cm)
PPT Slide
Lager Image
DBH, diameter at breast height.
The types of vegetation that become established in particular regions depend upon numerous factors, such as parental rock materials or topography, as well as the opportunities that make species distribution amenable. Even under similar environmental conditions, forests in a certain area can comprise of a mosaic of stands with different successional stages and vegetation types. This results from not only natural or artificial methods of regeneration, but also from large- or small-scale disturbances, the frequencies of those events, and the ways in which sites recover from such challenges.
The forests within Odaesan National Park are heterogeneous, but trees of at least 100 years old are widely distributed here, suggesting that large-scale harvests or forest fires have not taken place for the time being. This assumption is based on signs of selective logging for certain species and scattered clumps that have regenerated via sprouting. Fires might have been a threat in the past; however, at present it probably is not true in that park because the most common species on that mountain have proven to be highly resistant ( Choung et al. 2004 ). Furthermore, these forests have been protected by rigorous forest management policies since the 1970s ( Odaesan National Park Service 2008 ). Therefore, natural mortality and occasional high winds are the major disturbances that now form canopy gaps. The development of such gaps is largely a function of forest type, the prevailing disturbance regime, and geographical location ( Foster 1988 ). Daegwallyeong, an area that borders this park, is known in Korea for having very strong winds (average speed of 5.8 m/ s), a velocity that is second to Jeju Island’s 8.9 m/s ( Kim 2005 ). Because of that, the region is now the site of a wind farm. The high frequency and strength of these winds mean they have the potential to also cause major disturbances. Odaesan National Park is topographically vulnerable to wind damage because of its high elevation, steep slopes, and shallow soils on numerous scree sites. Moreover, when strong winds are accompanied by heavy rainfall, as it happened in October of 2006, the saturated soil becomes unstable, causing tall trees to fall, as they act as masts ( Clinton and Baker 2000 ).
In both of our forest types, canopy gaps tended to form on the slopes, suggesting that such locations are more affected by strong winds than mountain ridges or flat areas ( Kim 1996 ). The direction in which gap-makers fall is influenced by topography and the type and extent of the disturbance ( Cho 1992 ). In particular, because trees on flat land are considerably affected by wind direction, they tend to fall in a certain direction that makes it possible to estimate the severity of a particular disturbance ( Falinski 1978 ). When no specific disturbance has occurred, however, the fall direction is largely influenced by topography. Cho (1992) showed that in the neighboring area of Gwangneung Natural Forest at Soribong, most of the dead trees fell along the slope aspect in the absence of any disturbance. However, we found that trees growing on northeast-facing slopes in our mixed and Quercus forests tended to fall primarily to the southeast (86%) and southwest (90%), respectively. This suggested that the direction of tree-fall is affected more by wind rather than the slope.
Gap sizes in the mixed forest averaged 205.0 m 2 (75-442 m 2 ). This is approximately similar to the 246 m 2 reported from a study of deciduous broadleaf trees in a mature forest at Gwangneung ( Cho 1992 ), where the vegetation structure was almost the same as what we recorded in our current survey. In contrast, our Quercus forest had gaps averaging 86 m 2 (23-217 m 2 ), which was less than half the size of those measured in our mixed forest. We might attribute this variation to the difference in the number of gap-makers per gap, i.e., 2.8 in the mixed forest compared with 1.4 in the Quercus forest. Because the canopy of a single large tree covers 30-40 m 2 ( Park 2001 ), the gaps formed in our forest types could be considered relatively large (given the number of tree-falls) and might be related to species, height, and age. Trees of A. nephrolepis were the most frequently damaged in both forest types, even though the mixed forest also included many specimens of A. holophylla . Trees of the latter species can be 30 m tall ( Kim 2006 ). They also tend to take up more air space because they have larger canopies. In fact, the reason that the mixed forest had more gap-makers was because trees that were downed by strong winds there created a chain reaction that caused the other trees to fall along the slope. This was especially true for taller trees of A. holophylla , which were more heavily damaged on steeper slopes that comprised mostly of stony soils.
In the mixed forest, the majority of windthrown gapmakers belonged to A. nephrolepis (38.6%) and A. holophylla (22.7%). However, in its reference, i.e., the undamaged forest nearby, A. holophylla accounted for 6.4% and A. nephrolepis for only 0.2% of all trees, while the remainder was broadleaf species such as A. pseudo-sieboldianum and T. amurensis . This suggested that the two Abies species are more susceptible to wind damage. Altogether, 60.0% of the A. nephrolepis and 81.8% of the A. holophylla trees were uprooted; these are rates much higher than for any other tree species at that location. In studies conducted on the same forest, the method of death has varied by species ( Kanzaki and Yoda 1986 ) and those that were shallow-rooted have been easily uprooted ( Ruel et al. 2001 ). Thus, considering the lack of deep soil on our study sites, it is not surprising that those two shallow-rooted species (mean rooting depth of 138 cm for A. holophylla in the mixed forest) would be more susceptible to windthrow ( Lee et al. 2006 , Jeon 2009 ). Clinton and Baker (2000) have demonstrated that large trees are more prone to falling because they act as masts in very windy conditions. Here, the average diameter for trees downed directly by wind was larger than for those of the same species that were growing in the undisturbed reference forests. For A. nephrolepis , we cannot conclude the same because we were unable to make any valid comparisons due to the reference forest having only two trees of that species.
The undamaged sites within the Quercus forest were dominated by several broadleaf species, e.g., Q. mongolica , A. pseudo-sieboldianum , and T. amurensis , whereas A. nephrolepis occupied only 7.3% of the total density. Nonetheless, trees of that coniferous species, with their larger stem diameters, succumbed to windthrow more frequently, most likely due to morphological characteristics already discussed for the mixed forest.
A singularly strong wind accompanied by a blast of rainfall selectively uprooted trees of A. nephrolepis and A. holophylla at Odaesan National Park. These shallow-rooted conifers were growing in an area where the soil was shallow. Those conditions contributed to their falling in relatively higher proportions compared with other species on those sites. A secondary cause of death was having their branches broken when nearby broadleaf trees fell during the storm. Nagel and Diaci (2006) found that Abies alba was more susceptible than Fagus sylvatica to intermediate wind disturbance in Slovania. However, they discussed that tree size (DBH) was more important than the species. In a way, this is consistent with our study in that for some species, larger trees were more susceptible. However, Q. mongoica and B. schmidtii , that were thicker than those of reference forests had no windthrow at all. Therefore, we think that the susceptibility of the Abies species is a combined result of species, tree size (particularly height) and rooting depth, even though we cannot support this argument statistically due to the small number of trees.
Such small-scale disturbances alter site conditions and change the levels of resources, including light and moisture available for the remaining trees to grow. These scenarios also lead to the rapid regeneration of the existing canopy species or saplings and seedlings that are found in the understory layer according to the gap size.
Overall, these findings suggest that A. nephrolepis and A. holophylla are particularly susceptible to high winds because of their great heights and shallow root systems.
This work was supported by national parks of Korea and the Odaesan National Park Office in 2007, and by a 2014 research grant from Kangwon National University (C1011745-01-01).
Barden LS 1981 Forest development in canopy gaps of a diverse hardwood forest of the southern Appalachian Mountains Oikos 37 205 - 209    DOI : 10.2307/3544466
Barden LS 1989 Repeatability in forest gap research: studies in the Great Smoky Mountains Ecology 70 558 - 559    DOI : 10.2307/1940204
Boerner REJ , Cho DS 1987 Structure and composition of Goll Woods, an old-growth forest remnant in northwestern Ohio Bull Torr Bot Club 114 173 - 179    DOI : 10.2307/2996127
Bormann FH , Likens GE 1979 Pattern and Process in a Forested Ecosystem: Disturbance, Development, and the Steady State based on the Hubbard Brook Ecosystem Study Springer-Verlag New York, NY
Canham CD , Loucks OL 1984 Catastrophic windthrow in the presettlement forests of Wisconsin Ecology 65 803 - 809    DOI : 10.2307/1938053
Cho DS 1989 Regeneration of oak and the disturbance pattern in hardwood forests and oak savannas in Ohio. PhD Dissertation The Ohio State University Columbus, OH, USA
Cho DS 1992 Disturbance regime and tree regeneration in Kwangnung natural forest Korean J Ecol 15 395 - 410
Cho DS , Boerner REJ 1991 Canopy disturbance patterns and regeneration of Quercus species in two Ohio oldgrowth forests Vegetatio 93 9 - 18
Choung Y , Lee BC , Cho JH , Lee KS , Jang IS , Kim SH , Hong SK , Jung HC , Choung HL 2004 Forest responses to the large-scale east coast fires in Korea Ecol Res 19 43 - 54    DOI : 10.1111/j.1440-1703.2003.00607.x
Clinton BD , Baker CR 2000 Catastrophic windthrow in the southern Appalachians: characteristics of pits and mounds and initial vegetation responses For Ecol Manage 126 51 - 60    DOI : 10.1016/S0378-1127(99)00082-1
Falinski JB 1978 Uprooted trees, their distribution and influence in the primeval forest biotope Vegetatio 38 175 - 183    DOI : 10.1007/BF00123268
Foster DR 1988 Disturbance history, community organization and vegetation dynamics of the old-growth Pisgah forest, south-western New Hampshire, USA J Ecol 76 105 - 134    DOI : 10.2307/2260457
Greenberg CH , McNab WH 1998 Forest disturbance in hurricane-related downbursts in the Appalachian mountains of North Carolina For Ecol Manage 104 179 - 191    DOI : 10.1016/S0378-1127(97)00246-6
Jeon M 2009 Canopy gaps created by strong wind and vegetation regeneration in Mt. Odae National Park. MS Thesis Kangwon National University Chuncheon, Korea
Kang SJ , Choi CS 2000 Regeneration process in gap of Quercus mongolica forest J Ecol Environ 23 1 - 8
Kanzaki M , Yoda K 1986 Regeneration in subalpine coniferous forests II. Mortality and the pattern of death of canopy trees Bot Mag Tokyo 99 37 - 51    DOI : 10.1007/BF02488621
Kim KH 2005 Precise Investigation on Domestic Wind Resources and Research on the Enhancement for the Windfarm Development Technology in Korea. Ministry of Trade Industry and Energy Gwacheon
Kim SY 1996 Comparison of environmental factors and herb responses between gaps and non-gaps in Mt. Jumbong. MS Thesis The Catholic University of Korea Bucheon, Korea
Kim S 2006 Vegetation structure and spatial pattern of some dominant tree species at a mixed forest of Abies holophylla - broadleaved trees in Mt. Odae National Park. MS Thesis Kangwon National University Chuncheon, Korea
2008 Korea Meteorological Administration
Lawton RO , Putz FE 1988 National disturbance and gap phase regeneration in a wind-exposed tropical cloud forest Ecology 69 764 - 777    DOI : 10.2307/1941025
Lee KJ , Han BH , Choi JW , Choi IT , Hong SH , Bae JH , Kim JS , Ki KS , Gwak JI , Yoo EY , Jang JH , Lee SH 2006 Study on the preservation of Abies holophylla forests at Woljeong district Odaesan National Park Office Pyeongchang, Korea
Kim S , Shin Y , Choung Y 2012 Spatial pattern and association of tree species in a mixed Abies holophylla-broadleaved deciduous forest in Odaesan National Park J Plant Biol 55 242 - 250    DOI : 10.1007/s12374-011-0338-2
Lorimer CG 1977 The presettlement forest and natural disturbance cycle of northeastern Maine Ecology 58 139 - 148    DOI : 10.2307/1935115
Nagel TA , Diaci J 2006 Intermediate wind disturbance in an old-growth beech-fir forest in southeastern Slovenia Can J For Res 36 629 - 638    DOI : 10.1139/x05-263
2008 Monitoring of natural resources Odaesan National Park Service Pyeongchang, Korea
Park MY 2001 A study of gap dynamics in Mt. Jumbong. MS Thesis The Catholic University of Korea Bucheon, Korea
Peterson CJ , Pickett STA 1990 Microsite and elevational influences on early forest regeneration after catastrophic windthrow J Veg Sci 1 657 - 662    DOI : 10.2307/3235572
Ruel JC , Pin D , Cooper K 2001 Windthrow in riparian buffer strips: effect of wind exposure, thinning and strip width For Ecol Manage 143 105 - 113    DOI : 10.1016/S0378-1127(00)00510-7
Runkle JR 1981 Gap regeneration in some old-growth forests of the eastern United States Ecology 62 1041 - 1051    DOI : 10.2307/1937003
Runkle JR 1982 Patterns of disturbance in some old-growth mesic forests of eastern North America Ecology 63 1533 - 1546    DOI : 10.2307/1938878
Shin SS , Park SD 2006 Damage caused by a blast of wind accompanied by heavy rainfall and high seas in October 2006 in the east coast regions of South Korea Water Fut 39 49 - 56
White PS , Pickett STA , Pickett STA , White PS 1985 Natural disturbance and patch dynamics: an introduction;The Ecology of Natural Disturbance and Patch Dynamics Academic Press San Diego, CA 3 - 13