Wind-conditioned 20th century decline of birch treeline vegetation in the Swedish Scandes.
Key words: Betula pubescens ssp. tortuosa, deflation, drought, models, reindeer, retrogression, Swedish Scandes, treeline, warming, wind
R[ETH]SUM[ETH]. Cette etude porte sur un mode frequent, bien que non dominant, de changement de la limite des arbres dans les Scandes suedoises au cours du siecle precedent. Durant les 30 dernieres annees, on a suivi le declin dans la densite d'un peuplement de bouleaux pubescents subalpins (Betula pubescens ssp. tortuosa) qui etaient exposes au vent. Le resultat global comprenait une importante mortalite individuelle non compensee ainsi qu'une baisse radicale dans la taille des bouleaux survivants. La datation au radiocarbone de restes subfossiles de bouleaux trouves in situ dans un lieu voisin mais plus venteux a revele qu'un peuplement s'etait completement effondre au cours du siecle dernier ou C peu pres. On en deduit que les peuplements de bouleaux existants et disparus representent differentes phases d'un processus ininterrompu d'effondrement du niveau de peuplement, qui aurait son origine dans la perturbation causee par le renne durant l'ultime phase du petit ege glaciaire. Ce processus s'est ensuite poursuivi de facon plus ou moins autogene dans la direction du vent en raison de la nature du site qui etait expose au vent et C la secheresse. Un accroissement de la circulation du vent d'ouest et une diminution de l'humidite du sol (fonte des neiges precoce) au cours du siecle dernier pourraient avoir ete des facteurs contributifs, bien que cela demande une etude plus approfondie. Sur un terrain tres expose au vent, un siecle de rechauffement important n'a pas ete suffisant pour neutraliser le declin du bouleau. Les resultats soulignent la conclusion C savoir que, dans certaines circonstances, le vent et les effects ecologiques et physiologiques connexes sont les facteurs primordiaux qui determinent la position et la structure de la limite des arbres. Ce sont lC des connaissances fondamentales pour la creation de modeles du changement de la limite des arbres, modeles realistes C l'echelle du paysage, dans un avenir en rechauffement.
Mots cles: Betula pubescens ssp. tortuosa, deflation, secheresse, modeles, renne, retrogression. Scandes suedoises, limite des arbres, rechauffement, vent
Traduit pour la revue Arctic par Nesida Loyer.
In the Swedish Scandes, climate warming (1[degrees]C over the 20th century) has evoked upward shifts of the treeline as great as 150-165 m at some sites (Kullman, 2001, 2004d). This process is quantitatively paralleled elsewhere in the Northern Hemisphere (Kremenetski et al., 1999; Meshinev et al., 2000; Butler and Dechano, 2001; Munroe, 2003) as a plausible manifestation of broad-scale climate change. Obviously for the same reason, emergence of new stems within the advance zone (between the old and new treelines) is now a conspicuous process in many instances (Butler and Dechano, 2001; Kullman, 2001, 2004d; Lloyd and Fastie, 2003). Notably, however, most sites display upward treeline shifts smaller than those cited above, or no shifts at all (Kullman, 1979, 2001). Apparently, treeline positions (m a.s.l.) and structures are site-specifically constrained and modulated by different combinations of local and regional climatic forcing agents. Such mechanisms warrant closer investigation. Likely candidates for such agents relate to topoclimatic features such as strong wind action, extreme snow, and soil conditions. The current operational efficiency of this complex of agents is highlighted by the existence of patches within the treeline ecotone with actively regressing or totally denuded tree cover, ground vegetation, and topsoils, typically on windward sites of minor hillocks. Recent recolonizations by trees or other plants are virtually lacking and seem to be prohibited by local climatic harshness and associated deficiency of soil moisture and essential nutrients. Although these features are only minor parts of the total treeline landscape, they were already being observed frequently in the treeline ecotone more than 30 years ago (Kullman, 1997). They contrasted sharply with the 75-100 m elevational advance of the nearby birch treeline since the early 20th century and in filling of birch stands in more sheltered positions (Kullman, 1979). Over the past century, these regressive phenomena have been more or less explicitly described in the scientific literature (e.g., Sernander, 1905; Lundqvist, 1948; Rudberg, 1968; Holtmeier et al., 2003, 2004) from various parts of the Fennoscandian treeline landscape. In fact, processes of this kind seem to have more general relevance in alpine and Arctic regions with a more or less oceanic climate (e.g., Robertson, 1993; Grishin et al., 1996), but occasionally also in more continental regimes (Holtmeier et al., 2004).
In the perspective of the past century's well-documented warming (all seasons) in northern Sweden (Alexandersson, 2002), regressive processes of this kind may seem counterintuitive (cf. Grace et al., 2002), and their full comprehension presupposes a historical approach to the analysis. The present study seeks to contribute to a more complete understanding of this particular facet of treeline evolution by analyzing and monitoring the recent and subrecent history of arboreal vegetation in a typical retrogressional patch in the subalpine birch forest belt. Comprehension of this issue is essential for generation of realistic and detailed landscape-scale models of treeline and mountain woodland evolution in a world expected to warm beyond historic precedence during the next 100 years (IPCC, 2001; Raisanen et al., 2004).
The study was carried out in the southern Swedish Scandes, province of Jamtland (Fig. 1). A site representative of the processes focused on was located on the lower E-facing slope of Mt. Storsnasen (Fig. 2). This mountain reaches 1463 m a.s.l., with the adjacent floor of the Handolan River valley around 670 m a.s.l. The nearest meteorological station is Storlien/Visjovalen at 642 m a.s.l. and about 20 km to the northwest. The region's moderately oceanic and humid climate is due to its proximity to the Atlantic Ocean and the existence of low passes in the west. Mean temperatures (1961-90) are -7.6[degrees]C for January, 10.7[degrees]C for July, and 1.1[degrees]C for the year. On a yearly basis, the predominant wind direction is westerly (30%), which at the study site manifests as strong downslope winds (Kullman, 1979). The most frequent winds are W-S in winter and W-NW in summer (Raab and Vedin, 1995). Mean annual precipitation totals 850 mm for the same period. The bedrock of amphibolites is well covered by glacial till and peat up to or slightly above the birch treeline.
Climate warming in all seasons has characterized the past century. The summer period (June-August) has warmed by about 0.1[degrees]C per decade. Of all seasons, spring (March-May) shows the most consistent temperature rise (0.15[degrees]C per decade), which implies earlier snowmelt and onset of the growth period (Alexandersson, 2002). Drying-out of alpine/subalpine soils is a general consequence (Kullman, 2004a and literature cited therein).
The local treelines (the upper limit of 2 m high trees) are positioned at 800 m a.s.l. for mountain birch (Betula pubescens Ehrh. ssp. tortuosa (Ledeb.) Nyman), 720 m a.s.l. for pine (Pinus sylvestris L.), and 820 m a.s.l. for spruce (Picea abies (L.) Karst). The forest-alpine tundra transition (treeline ecotone) is dominated by mountain birch woodland, interspersed with patches of treeless alpine tundra and mires that increase in size and coalesce as altitude increases.
MATERIALS AND METHODS
Three plots were used to examine a sequence of birch decline (Fig. 2). In 1972, a 10 X 10 m permanent monitoring plot (Plot A) was established on the W-facing flank of a small hillock within the major E-facing slope of Mt. Storsnasen (725 m a.s.l., 63[degrees]13' N; 12[degrees]24' E). The plot has an elevational amplitude of about 5 m and is exposed towards prevailing westerly winds. It was placed in a representative portion of a local mountain birch stand that seemed to be in a stage of active demise and frontal retraction. The edge of more or less dying trees coincides with variously distinct wind deflation scars encroaching into the intact vegetation and soil cover (Fig. 3). The entire hillock is surrounded by a sloping and virtually treeless mire. The soil is sandy and dries rapidly during the summer since no supply of soil water from higher elevations takes place.
West of the erosion front is a treeless area, recently colonized with sparse alpine tundra, which showed evidence of strong cryoturbation (needle ice, frost heave, mud boils) and wind deflation of the topsoil. This area was virtually littered with in situ birch stumps in various stages of decay that clearly suggested a fairly long prehistory for the current phase of tree demise. All wood remnants that could be recovered here were sampled for radiocarbon dating within a 10 X 10 m plot (Plot B) fringing the western limitation of Plot A (Fig. 2). Since all birch remnants were strongly decayed, tree rings were not discernible, which excluded dendrochronological dating.
[FIGURE 1 OMITTED]
A closed ground cover with dominant Empetrum hermaphroditum and subsidiary Betula nana, Calluna vulgaris, Vaccinium myrtillus, Deschampsia flexuosa, Pleurozium schreberi and Hylocomium splendens is also present in Plot A. In Plot B, the ground vegetation is discontinuous. Large spots display bare mineral soil, interspersed with small clones of Loiseleuria procumbens, scattered specimens of Arctostaphylos alpinus, Juncus trifidus, Carex bigelowii, Ranunculus glacialis (temporarily) and fragments of reindeer lichens (Cladina spp.).
On the somewhat steeper E-facing, lee slope of the focused hillock, a dense, vigorously growing birch stand prevails. The predominant ground layer species is Vaccinium myrtillus. During the winter, the birch trees here are virtually buried in a 1.5-2.5 m deep snowdrift that usually remains until mid-June, or even longer in some years. In 2003, the age structure of this population was assessed within a 10 X 10 m quadrat (Plot C), by coring and sawing (trunk/root junction) all stems higher than 1 m (Fig. 2). Tree rings were counted in the laboratory using a stereomicroscope.
[FIGURE 2 OMITTED]
[FIGURE 3 OMITTED]
Radiometric dating of the birch remnants was carried out by the Radiocarbon Dating Laboratory in Stockholm (ST) and Beta Analytic Inc., Miami (Beta). All dates are given as radiocarbon years BP (= AD 1950). The low age of most samples (all less than 250 radiocarbon years) implies that calibration to calendar years is seriously inaccurate. This relates to particularly marked fluctuations in the atmospheric [.sup.14]C levels since about AD 1650 (Stuiver and Pearson, 1986). For this reason, the radiocarbon-dating laboratories report the ages in fairly broad and imprecise intervals. The presence of bark made identification to species (mountain birch) unambiguous.
In mid July 1972, all living birches within Plot A were entered on a sketch map and tallied with respect to maximum living height. On five subsequent occasions, at the same time of year in 1988, 1995, 2001, and 2003, the individual birches were located again and re-measured. In addition, we carefully scrutinized the plot for emergence of new birch recruits. These data provide the basis for evaluation of 31 years of demographic and size evolution.
Since late June 1996, ground temperature measurements within the central part of plot A have been carried out regularly (about once a month), using three soil temperature probes (resistance thermistors of the brand TO-03R) with the sensors installed at the interface between organic and mineral soil. At this depth (25 cm), short-term fluctuations are damped, and the current readings should quite accurately integrate the true soil temperature regime over the same intervals (cf. Harris, 2001). Snow depth in all three plots was also assessed at the time of these measurements. All these data form parts of a more extensive monitoring program and are only summarily reported here.
Along 3 m of the scarp between stripped coarse gravel and intact vegetation/soil at the interface between Plots A and B, the rate of erosion has been assessed at regular intervals since 1977. The annual retraction of this front has been monitored by measurements from six fixed sticks.
Demography and Vitality of Declining Birch in Plot A
During the period from 1972 to 2003, the number of living individual birches decreased from 44 to 31 (about 30%). No recruits (genets) were recorded during the same period in plots A and B. The mean height of all individual birches decreased at a fairly constant rate from 1.78 [+ or -] 0.65 m to 0.70 [+ or -] 0.58 m, a reduction of about 60%. The number of tree-sized birches (>2 m tall) decreased from 22 to 1 (95%). In no case have demised stems of this size-class been succeeded by equally tall basal sprouts.
Over the entire observation period, the birches have provided a conspicuous impression of low vitality, showing a multitude of dead twigs and short annual shoots. Most individuals had signs of wind deformation, such as leaning stems without twigs on the W-facing sides of their crowns. The height of the birches diminished from east to west within the plot--that is, against the prevailing wind direction.
Radiocarbon Dates from Plot B
A total of 36 subfossil birches were recovered and radiocarbon-dated within the treeless plot. They all appeared in situ as basal trunk/root sections, either well preserved in small, residual raw humus patches or lying more or less exposed on the bare mineral soil. In most cases, they seemed to represent quite small trees (basal diameters of 5-8 cm), closely resembling the size distribution of the currently living population in Plot A. The obtained ages span somewhat less than the past 250 radio-carbon years (Table 1). Tentative calibration implies that the trees died after the 16th century and in some cases even after AD 1950. The relatively high degree of preservation of these specimens, renowned for decaying fully and rapidly if not covered by peat, may suggest that the majority date to the 20th and late 19th centuries. Further support for this view is provided by the fact that dating was carried out on entire stem cross sections, with a likely life span of at least 100 years. This implies a slight bias toward older ages for the obtained mortality dates. Table 1 illustrates a tendency for the youngest ages to cluster near the current erosion front, at the interface between Plots A and B.
Current Erosion Rates
From 1977 to 2003, the annually surveyed erosion front between intact vegetation (Plot A) and denuded mineral soil (Plot B) retreated at a constant average rate of 2 cm per year, or about 0.5 m in that time. The dieback process involves winter killing by frost desiccation and abrasion by windblown snow and ice particles of the most exposed rim of plant cover, chiefly Empetrum. Subsequent erosion of this rim during spring and early summer is followed by dissipation of organic soils and the finer fractions of the top mineral soil by wind and rain action. In 1995, a small, prostrate, birch tree, growing 6.9 m outside the front (in Plot B), displayed 71 tree rings at the base. Conceivably, it became established and grew to tree size in intact vegetation well within the front (Fig. 4). It follows that, over less than 70 years, stand decline and erosion of ground cover and soil have proceeded by c. 7 m horizontally. Moreover, some roots from living trees extended 2-3 m into the deflation area of Plot B. Apparently, these data indicate that the entire sample plot has been denuded over the past century or so.
Soil Temperatures and Snow Regimes
During the period 1996-2004, maximum summer soil temperatures in Plot A, usually occurring in early August, ranged between 7.1[degrees] and 10.8[degrees]C. The years 2002 and 2003 displayed by far the highest records. Typically, freezing at the 25 cm level took place during December and thawing in the first half of June. The latter phenophase (and leaf unfolding) is one to two weeks later than in more sheltered and snow-rich birch stands at the same elevation. Minimum winter temperatures (early to mid March) varied over the years between -0.5[degrees] and -1.6[degrees]C. On a regional scale, the winters 1995-2003 were milder than the reference normal (1961-90), but there is no obvious trend during this short period (Alexandersson, 2002).
Strong wind exposure implies that the snow cover has been thin or periodically absent during the winter in both Plot A and Plot B. Within Plot A, the maximum snow depth, usually occurring in March, is about 15-20 cm. Plot B used to be snow-free or lightly dusted. Occasionally, the ground in Plot B is covered with a more or less well-developed ice crust. Evidence seen during casual observations in spring (April-May) indicates that the soil surface in this plot is subjected to strong diurnal freeze/thaw cycles. In plot C, a deep snow pack (> 2 m) accumulates during the winter and usually remains until after mid-June.
Birch Age Structure within Plot C
Most birches within the plot are multi-stemmed individuals, and therefore the age structure is based on more than one stem for each individual (Fig. 5). The oldest living stems date back to the late 19th century. The presence of a few decaying stumps from prior stout trees suggests that the population has a longer continuity than that, although the prevalence of young and tiny stems suggests that stand density has increased substantially during the past century. The presence of quite tall and declining specimens of light-demanding Juniperus communis also indicates a former more open structure.
[FIGURE 4 OMITTED]
Regeneration, both establishment of new individuals from seed and emergence of new basal sprouts, peaked in the 1930s and then declined over the following decades until a resurgence took place in the 1990s. In addition, virtual absence (< 1 %) of dead standing stems lends this stand a vital and expansive appearance, which is further enhanced by exceptionally long top-shoots (20-30 cm) during the years 2002 and 2003.
Since 1972, the birth population in Plot A has declined by 60% in living height. In addition, the substantial individual mortality (30%) is not balanced by any recruitment of new birch individuals. At this rate, this birch stand could become entirely exterminated well before the close of the present century. Much earlier, the residual population will be reduced to an assemblage of tiny basal sprouts emerging from the decaying stumps of previously tree-sized stems. As the size of the birches and the density of the stand diminish, wind shelter and snow retention are likely to decrease substantially (cf. Hiemstra et al., 2002). In addition, as the ground becomes increasingly smooth and level through wind erosion of the ground cover and organic top soil, the potential for intraspecific, interspecific, and microsite facilitation decreases, and birch establishment is prohibited (cf. Smith et al., 2003). Taken together, these circumstances may trigger a feedback loop that speeds up complete demise.
The lack of seed regeneration is not likely to be a consequence of poor seed viability in the treeline ecotone. On the contrary, this quality has improved substantially over the past 15 years in the study area (Kullman, 2004c). Moreover, mountain birch is currently regenerating quite freely in more sheltered sites with ample soil moisture, even high above the current treeline (Kullman, 2002, 2004a, c). Thus, the regeneration process does not seem to be constrained by insufficient heat. Instead, failure to regenerate is more likely to result from soil moisture and nutrient deficiency within this highly wind-exposed setting. The site is largely deprived of finer soil fractions and has a tendency, further aggravated by the erosion process, to dry out early in the summer. The sensitivity of mountain birch seedlings to soil drought and nitrogen deficiency has been well established experimentally (Kullman, 1984; Karlsson and Weih, 2001). A landscape-scale manifestation of this relationship is provided by the 20th-century history of the birch treeline in this region (Kullman, 1979). It was found that snow deflation sites with consequent and enhanced shortage of meltwater supply during the summer did not display upshifts of the treeline in response to the climatic warming trend. In addition, the recorded minute snow cover protection, associated low soil winter temperatures, and frequent freeze-thaw cycles during spring and autumn enhance the hostility of this environment with respect to establishment and survival of birch seedlings. Environmental conditions of this kind may be particularly damaging to fine roots of seedlings and saplings trying to establish here (cf. Holtmeier, 2000). Against this background, the general trend of decreasing soil moisture (see above) may have contributed to the birch demise in this particularly drought-prone setting.
[FIGURE 5 OMITTED]
Reindeer grazing and trampling are another potential obstacle to regeneration and an initiator of soil erosion, since these snow-poor sites are the only grazing grounds during the spring (Rudberg, 1968; Kullman, 1997; Oberg, 2002). However, reindeer are ancient and integral parts of this ecosystem, and the size of the herds has not changed significantly over the past century. A thorough review of existing data from the Swedish Mountains provides no evidence of large-scale or severe vegetation degradation or soil erosion during the past few decades that can be attributed to reindeer husbandry (Moen and Danell, 2003). Thus, reindeer activity is not likely to be the driving force behind the birch forest demise studied here. Although scarification and removal of vegetation and soil by reindeer action in windward positions may have contributed to initiating the process in the distant past, its progression seems to depend primarily on the extreme character of the local climate, especially the wind. Certain support for the contention of reindeer disturbance as the triggering agent is provided by Smith (1920), who documented extensive destruction of exposed lichen heath in obvious response to grazing and trampling of anomalously large reindeer herds in this area during the first decade of the 20th century. Similar observations were reported a few years earlier (Sernander, 1905). Other potential initiators have been considered, such as outbreaks of defoliating insects, or the "fir wave" dieback phenomena observed in North America (e.g., Reiners and Lang, 1979). The first option is not supported by any observations reported in older descriptive accounts from this local area (Sernander, 1899; Smith, 1920; Tenow, 1972). The "fir wave" option is even less likely, since there is no regrowth behind the dying front to indicate cyclicity, and the resulting open spaces do not move over the hill slopes. Initial, catastrophic wind throw events are out of question, since practically all dated birch remnants are rooted in situ. A strong case for broad-scale causation mechanisms for the initiation and continuation (not the same) of the birch dieback is provided by the prevalence of the phenomenon described here in similar topographical situations, both nearby and elsewhere in northern Fennoscandia (see Introduction).
Conceivably, initiation is some kind of radical physical disturbance, and the balance of evidence suggests that reindeer action may have triggered the birch decline. Holtmeier et al. (2004) arrived at a similar conclusion with respect to the same type of processes in Finnish Lapland.
Since climate warming over the past century has not reversed the retrogressional trend of the birch at the study site, it must be inferred that particular local topoclimatic characteristics, wind exposure being the foremost, limit the studied birch population and its response patterns. The latter contention is strongly supported by the progressive and contrasting performance of the birch population in the nearby and much more sheltered Plot C.
It appears that the entire system in Plot A is rapidly approaching a stage where it will be pushed over its threshold of recovery. This is obviously what happened in Plot B, where a birch population similar to that currently existing in Plot A gradually died over 100 years or somewhat more--a period encompassing the close of the Little Ice Age cold episode (Grove, 1988) and the subsequent 20th century warming phase (Alexandersson, 2002). Analyses of long-term instrumental meteorological data reveal that the latter course of climate evolution in Scandinavia has been associated with a strong increase in westerly atmospheric circulation (Jonsson and Fortuniak, 1995; Alexandersson et al., 2000; Omstedt et al., 2004). The higher frequency of strong westerly winds, in combination with earlier snowmelt (Moberg et al., 2005), may have aggravated site conditions for birch, particularly at west-exposed sites like the one focused on here. This aspect should not be overstated, however, and it may well be that progressive birch decline has its roots in the Neoglacial climate cooling and associated treeline depression (Kullman, 1997, 2003; Holtmeier et al., 2004). After initial disturbance, possibly by reindeer, during this period, the process may have proceeded more or less autogenically in the most exposed sites, which strongly indicates the crucial importance of wind for treeline performance.
Conceivably, birch demise will stop as the front passes eastwards over the crest of the hillock at the upper (western) fringe of Plot C, where wind shelter and snow accumulation increase dramatically within a very short distance. Furthermore, birch growth here is likely to benefit from steady nutrient enrichment from the eroding soil, which is redeposited on this lee side (cf. Malanson and Butler, 1994).
The present results highlight complex interactions between climate and the heterogeneous physical landscape, which govern treelines and their responses to climate change (cf. Kupfer and Cairns, 1996; Holtmeier, 2000; Kullman, 2001; Malanson, 2001; Kjallgren and Kullman, 2002). These insights add to the rising uncertainty concerning direction and magnitude of treeline changes in a hypothetical warmer world (cf. Grishin, 1995; Risser, 1995; Crawford et al., 2003; Moore, 2003). Modeling of the development of the high-elevation arboreal landscape in a virtually unprecedented future climatic regime (IPCC, 2001) has to consider the local operation of mechanisms such as the one uncovered in the present study. Moreover, as potential tree limits rise towards higher and generally windier environments, accounting for the current type of counteractive mechanisms could reasonably become increasingly relevant (cf. Grace, 1997). This point is further substantiated since anticipated "greenhouse warming" may be associated with an even higher frequency of strong westerly winds (Davis, 1989; Andersen et al., 2001).
The present study strengthens the view that wind is an important and generally underrated ecological disturbance factor and modulator of local treeline patterns and positions (cf. Reiners and Lang, 1979; Davis, 1989; Grace, 1989; Komarkova and Wielgolaski, 1999; Seppala, 2004). For that reason, consistent climate warming will not evoke broad frontal displacement of vegetation belts at a common rate to increasingly higher altitudes (cf. Woodward, 1993). Primarily, expansion of subalpine forest vegetation will be patchily restricted to sheltered slopes with ample soil moisture, while it will proceed much more slowly (if at all) on wind-open, exposed sites. This scenario is analogous to tree-limit performance during the warm and dry early Holocene, when trees grew in isolated, sheltered patches 500-600 m above their current limits (Kullman, 2004b). Regional response patterns recorded empirically over the past century further support that contention, showing that the magnitude of climate-driven treeline advance relates to the degree of wind exposure and associated ecological conditions (Kullman, 1979).
This study was funded by the Swedish Research Council. Thanks are due to Anna-Karin Kullman for assistance in the field. I am most grateful to anonymous referees, who contributed to the clarity of the paper.
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LEIF KULLMAN (1)
(Received 14 September 2004; accepted in revised form 22 February 2005)
(1) Physical Geography, Department of Ecology and Environmental Science, Umea University, S-901 87 Umea, Sweden; firstname.lastname@example.org
TABLE 1. Radiocarbon dates of subfossil birch remnants within Plot B, listed according to the distance to the erosion front, i.e., the interface between Plots A and B. Radiocarbon Age Distance to the A/B Border Laboratory No. ([.sup.14]C yr BP) (m) Beta-5400 Post 0 0.2 Beta-91501 Post 0 0.2 Beta-91502 Post 0 0.3 ST-13622 < 250 0.4 Beta-99189 Post 0 0.5 Beta-99203 Post 0 0.5 Beta-99410 Post 0 0.7 ST-13616 < 250 0.9 Beta-99411 Post 0 1.3 Beta-106350 Post 0 1.4 Beta-106353 Post 0 1.8 Beta-106356 Post 0 2.6 Beta-108770 Post 0 3.0 ST-13610 < 250 3.1 Beta-106354 Post 0 3.4 Beta-99217 30 [+ or -] 60 3.5 Beta-86972 10 [+ or -] 70 3.5 Beta-99192 40 [+ or -] 50 3.9 Beta-99413 80 [+ or -] 60 4.1 Beta-160728 50 [+ or -] 60 5.0 Beta-99212 70 [+ or -] 60 5.2 Beta-106355 90 [+ or -] 80 5.3 Beta-106358 90 [+ or -] 50 5.8 Beta-99193 110 [+ or -] 60 6.4 ST-13628 < 250 7.1 Beta-91500 110 [+ or -] 50 7.5 ST-13610 < 250 8.0 Beta-91499 240 [+ or -] 50 8.1 ST-13620 < 250 8.2 ST-13617 < 250 8.9 Beta-99407 140 [+ or -] 50 9.1 Beta-99409 160 [+ or -] 80 9.2 ST-13615 < 250 9.3 Beta-180209 150 [+ or -] 60 9.3 Beta-106377 230 [+ or -] 60 9.5 ST-13607 < 250 9.6 ST-13614 < 250 9.8
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