Tree rings are thought to be a powerful tool to reconstruct historical growth changes and have been widely used to assess tree responses to global warming. Demographic inferences suggest, however, that typical sampling procedures induce spurious trends in growth reconstructions. Here we use the world’s largest single tree-ring dataset (283,536 trees from 136,621 sites) from Quebec, Canada, to assess to what extent growth reconstructions based on these - and thus any similar - data might be affected by this problem. Indeed, straightforward growth rate reconstructions based on these data suggest a six-fold increase in radial growth of black spruce (Picea mariana) from ~0.5 mm yr−1 in 1800 to ~2.5 mm yr−1 in 1990. While the strong correlation (R2 = 0.98) between this increase and that of atmospheric CO2 could suggest a causal relationship, we here unambiguously demonstrate that this growth trend is an artefact of sampling biases caused by the absence of old, fast-growing trees (cf. “slow-grower survivorship bias”) and of young, slow-growing trees (cf. “big-tree selection bias”) in the dataset. At the moment, we cannot envision how to remedy the issue of incomplete representation of cohorts in existing large-scale tree-ring datasets. Thus, innovation will be needed before such datasets can be used for growth rate reconstructions.
Anthropogenic greenhouse gas emissions have resulted in an unprecedented rise in atmospheric CO2 over the past decades1,2,3 and have led to rapid global warming4. Understanding the response of forests to these changes is important, as forests play a crucial role in the global carbon cycle5,6,7. However, evidence for long-term changes in growth, and possible drivers and mechanisms such as CO2 fertilization and temperature increases, remains poor. Changes occurring at northern latitudes may be of particular importance, as these regions experience the fastest rates of warming and are the second largest above-ground organic carbon store, after tropical forests8. Reported recent growth trends in this region disagree emphasizing the need for a better understanding of long-term historical changes in land vegetation cover and its functioning. This is especially important to predict the role played by forests in moderating future atmospheric greenhouse gas levels.
All approaches used to study the response of forests to environmental changes have their strengths and limitations. Among all, tree-ring data have the advantage of extending far back in time. In addition, they provide naturally annual records and can easily be obtained. They have thus been seen as a prime candidate to provide a long-term perspective of tree growth response to global environmental change9,10. Hence, such data have been used more and more over recent years for growth reconstructions11,12,13,14,15,16,17,18,19,20,21.
However, there is a large, underestimated problem with tree-ring data, namely that tree-ring sampling procedures can lead to spurious growth trends as sampled trees are not representative of the full cohorts of trees that lived in the past22,23,24,25. This is particularly apparent in tree-ring studies in which only living, dominant and codominant trees are sampled22,23,25. Among the various potential biases (see24,26), those arising from differences in tree growth rates have received much attention. In particular, if longevity differs between fast- and slow-growing trees, then biases may arise. Indeed, evidence suggests that fast-growing trees, which reach their maximum potential size sooner than slow-growing trees have a shorter lifespan27,28,29. Therefore, sampling only currently living trees leads to an underrepresentation of fast-growing trees in the earlier portion of the growth dataset, as those early born, fast- growing trees would have died before sampling (cf. “slow-grower survivorship bias”)23. As a result, tree-ring based growth reconstructions extending over long periods tend to be biased toward slow growth in the early part of the record. This creates an apparent increase in growth rate over time. In addition, classic tree-ring sampling approaches disproportionately favor larger trees, which introduces another bias. Young, slow-growing trees will not have reached the sampling diameter threshold, whereas fast-growing trees of the same age are larger and thus more likely to be sampled (cf. “big-tree selection bias”)23. As a result, fast-growing trees will be overrepresented in the more recent period. This further accentuates the apparent trend of increased tree growth in the most recent period. The existence of these biases has been demonstrated theoretically, using stochastic tree growth simulations23, and in real nature, for one single, small stand-scale tree-ring dataset25. However, we know little about how common these biases are, more generally, and to what degree they affect growth trend reconstructions in large-scale studies.
In this study, we use a unique dataset of tree-ring measurements from 283,536 trees sampled in 136,621 stands to analyse trends in radial growth over the last 250 years and assess to what extent growth reconstructions based on these data might be affected by the above-mentioned biases. This dataset comprises the world’s largest number of tree-ring samples collected according to standardised methods across a large geographic region (eastern Canada). We focus our analysis first on black spruce (Picea mariana), which is the most abundant tree species in this dataset (Fig. 1), and then verify if the same pattern can be observed for 12 other tree species.
We here also test to what degree biases arise when using different tree-ring detrending approaches. The study of external (climatic) forcing on tree growth requires the removal of age- or size- related variation in growth rates, commonly referred to as ‘tree-ring standardisation’30. Various methods have been used to remove age -or size-related growth trends31. Traditional standardisation methods fit a curve to individual series and remove all variance at the individual tree level, including a substantial part of the long-term historical growth rate variation, which is exactly the variation of interest for studies on the tree’s response to CO2 and global warming. Thus, a growing number of studies have developed and used more conservative standardisation methods that maintain growth difference between trees (e.g. regional curve standardisation)32,33 or focused on raw, unstandardised or basal-area-converted ring widths time series15,16,17,20,21,34,35,36,37,38,39. Given that the magnitude of biases may differ depending on the choice of detrending method, we compare three different detrending methods. First, we simply focus on a fixed diameter or age range (cf. size or age class isolation detrending)31 to avoid the effect of declining radial growth with increasing tree age and size32,33. Then, we repeat this analysis using two common tree-ring standardisations, a traditional tree-level standardisation procedure (c.f. linear regression standardisation)30 and the increasingly advocated Reginal Curve Standardisation (RCS)33.
Results and Discussion
Simple averaging of juvenile growth rate of black spruce cohorts over the last 250 years indicates a six-fold increase in ring widths from means (±95% CI) of 0.40 ± 0.03 mm for tree cohorts in the 1760s to 2.63 ± 0.03 mm for those in the 1980s (Fig. 2). This rapid nonlinear growth increase is deceptively similar to the increase in atmospheric CO2 since pre-industrial times (R2 = 0.98, Fig. 2). Thus, it is tempting to attribute this trend to the effect of global change on forest productivity (through temperature changes or CO2 fertilization, for example). However, further analysis reveals that this interpretation is erroneous.
Assuming that a species-specific, size-dependent mortality rate exists and that the vast majority of trees dies before reaching a given ‘maximum’ diameter, then there will be an inverse relationship between growth rate and longevity (i.e., fast-growing trees will have a shorter lifespan than slow-growing trees)27,28,29. To estimate to which degree the difference in life-expectancy of fast- and slow-growing trees may have driven our results, we assumed that there exists a maximum diameter, Dmax, which trees reach before they die. We then estimated Gmax, the limiting maximum growth rate allowing trees to be still alive in 2012, the last year of sampling, as a function of past recruitment time (trecr):
where trecr is given in years AD. We estimated Dmax as the 99th percentile of diameters in the dataset, which is 298 mm diameter for black spruce (see Fig. S1). From the curve of Gmax as a function of recruitment year (Fig. 3, blue line), it is clear that there is a strong asymmetry across past time in growth rates of trees that are expected to be still alive in 2012 (all trees with growth rates and recruitment ages in the area below the blue line). Thus, among trees recruited far in the past, only very slow-growing trees will be part of living trees at a given year of sampling.
Another bias arises because living trees are usually not sampled uniformly across diameter classes. Indeed, the sampling protocol used in the field (see methods) probes only trees that have reached 91 mm in diameter (or 45.5 mm in radius) at a height of 1.3 m above ground level, thus excluding those individuals which have not yet reached the minimum diameter threshold (Dthresh). In an approach similar to the one above, we can express Gmin, the minimum mean growth rate which a tree needs to reach this minimum diameter threshold, as a function of recruitment time in the past:
Again, there is a strong asymmetry among trees with different growth rates across recruitment times in the past that make it into the sample of trees probed. This is because only trees with growth rates and recruitment ages above the red line in Fig. 3 will be sampled. Indeed, when recruitment years and mean growth rate of all black spruce trees of our dataset are added in the same figure (Fig. 3) they mostly populate the area between the red and blue lines. This gives strong support for our interpretation of the effects of a growth longevity trade-off and of a minimum sampling size threshold on growth rate reconstructions. Since the increasing trend of the blue and red curves does not result from any growth stimulation, it appears very likely that the convex shapes of growth vs. age relationships in Figs 2 and 3 are simply an artefact induced by these biases. The exact same pattern was observed for 12 other common boreal tree species showing that the bias observed for black spruce is widespread (Fig. S2).
The black spruce tree-ring dataset covers more than 33,000 sites over a large geographic region. It is thus ideal to probe the extent to which growth rates and tree age covary with environmental growing conditions, and to evaluate how this may cause biases in growth rate reconstructions. If growth rates and tree age are inversely related across our dataset, we expect to observe temporal shifts in the relative proportions of trees belonging to zones with different productivity (growth rates) in our sample. Indeed, we find that in our dataset tree growth in the northern and colder bioclimatic domain are lower and that trees reach older ages (114 years) when compared with southern and warmer territories, where growth rates are higher and tree ages are lower (69 years) (Fig. 4a–d). As a result of this, we see shifts in the relative proportions of trees in our dataset coming from these different zones over time, with a higher proportion (~80%) of slow-growing trees from less productive colder sites in the earlier period (e.g. 1760–1850), and higher proportions of fast-growing trees from warmer sites in recent periods (Fig. 4e). Similar patterns emerge when trees are stratified according to soil or crown cover with decreases in the proportion of trees growing on less productive soils (very shallow or very stony soils and soils with hydric moisture regime) and of trees from less productive, open lichen–spruce woodlands (26–40% crown cover) (Fig. S3e,j). These results indicate either that there are true strong temporal shifts in the relative recruitment of black spruce in different subregions, or that trees on more productive sites live shorter lives. Given the consistency in shifts of relative abundance across subregions stratified using intrinsically different environmental characteristics (i.e., climate, soil, crown cover), we argue that these changes in relative proportion of trees in the dataset coming from different subregions are indeed due to a trade-off between growth and longevity. Shorter tree longevity at the most productive sites results in lower abundance of trees at these sites in earlier periods. While this must drive part of the observed convex relationship between growth and recruitment year, restricting the dataset to a single bioclimatic zone, soil physical environment, or stand density class still results in strong biases in growth reconstructions (See Fig. S4). Similarly, we find that the biases still persist even when separating the dataset by the plot levels of disturbances, such as fire, or intervention history (thinning or harvesting) (Fig. S5). This analysis provides yet another warning against the use of tree-ring data to infer patterns of phenomena such as historical recruitment across large geographic regions or over long time periods40,41, as tree lifespan depends on productivity, and thus varies between sites.
Relative contribution of biases
To disentangle the relative contribution of the two biases, caused by absence of old, fast-growing trees and of young, slow-growing trees from the dataset, to the growth trends, we created a hypothetical steady state tree growth trajectory dataset. This dataset was constructed by shifting backwards and forwards in time, the lifetime mean annual radial growth data of all individual black spruce samples one year at a time for the period of 1757 to 2000 (from Fig. 3). By construction, for such a tree population, growth rate is constant over time (horizontal black line in Fig. 5, growth rate 1.1 mm yr−1). However if we sample only trees living in the year 2000 and restrict ourselves to trees with diameters larger than 91 mm, we observe a rapidly increasing mean radial growth rate (green data points, Fig. 5). If we now include all trees living in 2000 with diameters smaller than 91 mm (red dots in Fig. 5), the very large bias (‘big-tree selection bias’) during the more recent period (last 100 years) disappears. On the other hand, if we include all trees which were historically present but have died before 2000 (but not the trees alive in 2000 with a diameter less than 91 mm) then the large bias (‘slow-grower survivorship bias’) at the far end of the period (1750–1800) disappears. In summary, this analysis shows that the spurious trend in our data (green line in Fig. 5) is approximately to 80% driven by the big-tree selection bias (blue line) with the remainder driven by the slow-grower survivorship bias (red line). This is consistent with our previous predictions using stochastic tree growth simulations showing that the big-tree selection bias has the largest effect23. Importantly, even when including small trees, and thus avoiding the big tree selection bias altogether, we still find a five-fold increase in growth rates since 1750 due to the slow-grower survivorship bias. Nehrbass-Ahles et al.25 recommend that sampling all individuals in a population would satisfy the requirements for all growth studies, including long-term growth trend reconstructions, but our results clearly contradict this assertion.
Effect of data standardisation
Tree ring based studies aiming to estimate tree growth response to global environmental changes commonly apply standardisation methods, which are essential for the interpretation of tree-ring data in the context of global change responses. However, as we will demonstrate they either do not remove the two biases we describe here, or do remove the biases at the cost of losing the long-term signal. Existing standardisation procedures aiming at removing biological effects on growth rates due to tree ageing, or size-related changes in tree physiology31, can be classified roughly into two categories: (i) “population- or plot-level” detrending approaches, such as “Regional Curve Standardisations”, RCS32,33 or size class isolation methods31, which use a population or site-specific size- or age-related growth curve to detrend the individual tree series, and (ii) “tree-level” detrending approaches which use linear or negative exponential functions, or cubic smoothing splines to detrend individual tree-ring series34,42,43,44,45. In both approaches, growth rate anomalies are calculated as the difference (or ratio) between the original tree-ring width time series and the fitted (detrending) curve. The main differences between these approaches are the frequency band of variation retained and their susceptibility to the biases we described.
We examined the interplay of the main standardisation methods and biases described here. Firstly, our approach to examine growth in a particular size class falls into the first category, “population level detrending”. We had focused on only the smallest size class, and extended this to two larger size classes and to three different age classes (Fig. S6). This analysis shows that biases arise in all scenarios, but to a different degree (Fig. S6). The magnitude of the bias in ring width decreases slightly for larger size classes due to a diminished effect of the big-tree selection bias (cf. ref. 23). Using age classes instead of size classes shows largely similar patterns as using size classes (Fig. S6b). The observed biases also persist and are in some cases even greater when expressing growth as basal area increment instead of ring width increment, showing that apparent growth trends also depends strongly on the choice of growth metrics used (Fig. S6). Using a similar and widely applied approach for population level detrending, the Regional Curve Standardisation32,33, shows also strong biases (see Fig. S7c). In contrast, the second approach, tree level detrending, does fully remove the bias (see Fig. S7d), but it also loses the ability to detect historical long-term growth changes that extend beyond the length of individual growth series. Various intermediate approaches have been applied recently, such as using generalized additive mixed models to predict individual growth series from regional or plot-level expectation of age trends (modeled by negative exponential smoothing, for example)14,46, or using individual or multiple RCS curves according to individual growth rates of trees, plots, or sites (adaptive regional growth curve)47. Some of these approaches do remove part or most of this bias, but only at the cost of losing information about long-term growth rate changes. Unfortunately, no single detrending procedure yet exists that is able to simultaneously maintain long-term variation and correct for the bias observed here.
Some procedures such as sampling all living trees in a fixed plot, reduces the big-tree selection bias, but our results show that such adjustments of field sampling designs (cf. ref.25) do not resolve the problem arising from the trade-off between growth and longevity. At the moment, we see no fix to the problem arising from missing growth information of trees that died during the period of the growth reconstruction. Only a complete sample of the entire historical population allows truly unbiased reconstructions. Theoretically, this problem could be solved by sampling trees that died recently and are still easily recognisable or sub-fossil trees, stumps and logs23,24,25. However finding and sampling all individuals that were once present in the population is nearly impossible, and we thus conclude that systematic biases in historical growth rate reconstruction at the population- or stand-level are practically unavoidable. We therefore recommend great caution in interpreting low-frequency variation associated with historical growth reconstructions from tree rings of the types presented here.
In addition to the two biases detected here, other types of biases due to a non-uniform age structure of sampled trees (“non-uniform age bias”)26 and possible declines in growth rates of trees prior to death (“pre-death suppression bias”)24 may induce apparent negative growth trends over time. This further complicates the use of tree-ring data for long-term growth and climate reconstructions. Hence, preserving long-time scale environmentally related changes in tree-ring width data while removing age- and size- dependent variations and disentangling positive and negative biases remains one of the biggest challenges for historical growth rate and climate reconstructions22,23,48,49,50. We challenge theorists and demographers to come up with solutions to these problems. In the meantime, our results raise doubts about the validity of existing studies that suggest growth increases based on tree-ring analyses.
The study area corresponds to the forest territory below the current northern limit of the managed forest in Quebec, Canada. It covers approximately 580,000 km2, from 45° to 52° North with annual temperature and precipitation ranging from −2.6 °C to 7.4 °C and from 770 to 1,600 mm, respectively. The area includes various soil substrates and disturbance histories. At the beginning of the 20th century, logging activities were confined to the southern portion of the province (south of 49° north latitude), whereas they currently take place up to 51° North. Each year since the beginning of the 21st century, approximately 0.7% of the managed forest area has been harvested commercially. Besides forest management activities, fires and spruce budworm (Choristoneura fumiferana Clemens) outbreaks have been the main disturbances of forest dynamics over the last century51.
We compiled tree-ring measurement data acquired by the provincial forest inventory program in Quebec, Canada52. These programs include networks of both temporary and permanent sample plots, providing a comprehensive overview of existing forest resources. The third round of forest inventories took place from 1990 to 2002 and provided data from approximately 101,000 sample plots distributed throughout the provincial forest. The fourth round is currently being completed53. Circular plots (400 m2, radius = 11.28 m) were selected using a stratified random sampling protocol53. Along with stand and soil characterization, tree cores were sampled from 1996 to 2012 in both permanent and temporary sample plots according to strict sampling protocols53,54. The sampling procedure at the stand level is not entirely random, and biased toward intensive sampling of large trees. In each temporary sample plot, 3 trees (diameter at breast height [DBH] ≥91 mm) were sampled at a height of 1 m above ground level: 1 tree was selected randomly, another was selected randomly among the 4 biggest trees (in DBH) of the dominant species, and the last had the diameter closest to the mean diameter of the dominant tree species. In each permanent sample plot, up to 9 trees were sampled: 5 trees were selected randomly, 2 were selected randomly among the 4 biggest trees (in DBH) of the dominant species, 1 had the diameter closest to the mean diameter of the dominant tree species, and the last had a basal area at breast height closest to the 30th percentile of the distribution of stem basal area for the dominant species. In all cases, only one core per tree was sampled. In 2012, the database included tree-ring measurements of close to 365,000 trees from 42 species and 121,000 plots. Complete core sampling and measurements, mainly conducted to estimate site index, were limited to coniferous species and to the most abundant shade-intolerant deciduous species that generally form even-aged stands (Betula papyrifera Marshall and Populus sp.). Cores were dried, glued to a wooden tray, and sanded according to standard procedure55. Ring boundaries were first detected and identified under binocular magnification, then measured to the nearest 0.001 mm with the WinDendro image analysis system for tree-ring measurement (Regent Instruments Inc.). From this database, we first focused on black spruce (Picea mariana), the most abundant boreal tree species, which represents approximately one quarter of the 363,933 core samples (Fig. 1), then checked how patterns held up for the other 12 most abundant boreal species. To avoid problems inherent to stem asymmetry and bark thickness variability over time, we filtered samples using individual cumulative growth instead of field diameter measurements, in order to select only trees cumulating more than 45.5 mm of growth (sampling DBH threshold of 91 mm).
Raw provincially-owned data are available from the “Direction des inventaires forestiers du Ministère des Forêts, de la Faune et des Parcs” upon request. The Direction may be contacted at: email@example.com.
Tans, P. P., Fung, I. Y. & Takahashi, T. Observational constraints on the global atmospheric CO2 budget. Science 247, 1431–1438 (1990).
Keeling, C. D. et al. Atmospheric carbon dioxide variations at Mauna Loa Observatory, Hawaii. Tellus 28, 538–551 (1976).
Robertson, A. et al. Hypothesized climate forcing time series for the last 500 years. J. Geophys. Res. 106, 14783–14803 (2001).
IPCC. Climate Change 2014: Synthesis Report. (IPCC, Geneva, Switzerland, 2014).
Bonan, G. B. Forests and climate change: forcings, feedbacks, and the climate benefits of forests. Science 320, 1444–1449 (2008).
Friedlingstein, P. et al. Climate–carbon cycle feedback analysis: results from the C 4 MIP model intercomparison. J. Clim. 19, 3337–3353 (2006).
Huntingford, C. et al. Towards quantifying uncertainty in predictions of Amazon ‘dieback’. Philos. Trans. R. Soc. B Biol. Sci. 363, 1857–1864 (2008).
Pan, Y., Birdsey, Ra, Phillips, O. L. & Jackson, R. B. The structure, distribution, and biomass of the world’s forests. Annu. Rev. Ecol. Evol. Syst. 44, 593–622 (2013).
Zuidema, P. A. & Frank, D. Forests: Tree rings track climate trade-offs. Nature 523, 531 (2015).
Babst, F., Poulter, B., Bodesheim, P., Mahecha, M. D. & Frank, D. C. Improved tree-ring archives will support earth-system science. Nat. Ecol. Evol. 1, 1–2 (2017).
Beck, P. S. A. et al. Changes in forest productivity across Alaska consistent with biome shift. 14, 373–379 (2011).
van der Sleen, P. et al. No growth stimulation of tropical trees by 150 years of CO2 fertilization but water-use efficiency increased. Nat. Geosci. 8, 24–28 (2015).
Charney, N. D. et al. Observed forest sensitivity to climate implies large changes in 21st century North American forest growth. 19, 1119–1128 (2016).
Girardin, M. P. et al. No growth stimulation of Canada’s boreal forest under half-century of combined warming and CO2 fertilization. Proc. Natl. Acad. Sci. 113, E8406–E8414 (2016).
Matias, L., Linares, J. C., Sanchez-Miranda, A. & Jump, A. S. Contrasting growth forecasts across the geographical range of Scots pine due to altitudinal and latitudinal differences in climatic sensitivity. Glob. Chang. Biol. 23, 4106–4116 (2017).
Weiwei, L. U., Xinxiao, Y. U., Guodong, J. I. A., Hanzhi, L. I. & Ziqiang, L. I. U. Responses of intrinsic water-use efficiency and tree growth to climate change in semi-arid areas of north China. Sci. Rep. 8, 308 (2018).
Salzer, M. W., Hughes, M. K., Bunn, A. G. & Kipfmueller, K. F. Recent unprecedented tree-ring growth in bristlecone pine at the highest elevations and possible causes. Proc. Natl. Acad. Sci. USA 106, 20348–53 (2009).
Lebourgeois, F., Eberlé, P., Mérian, P. & Seynave, I. Social status-mediated tree-ring responses to climate of Abies alba and Fagus sylvatica shift in importance with increasing stand basal area. For. Ecol. Manage. 328, 209–218 (2014).
Silva, L. C. R. et al. Tree growth acceleration and expansion of alpine forests: The synergistic effect of atmospheric and edaphic change. Sci. Adv. 2, e1501302 (2016).
Kosiba, A. M., Schaberg, P. G., Rayback, S. A. & Hawley, G. J. Comparative growth trends of five northern hardwood and montane tree species reveal divergent trajectories and response to climate. Can. J. For. Res. 47, 743–754 (2017).
Silva, L. C. R., Anand, M. & Leithead, M. D. Recent widespread tree growth decline despite increasing atmospheric CO2. PLoS One 5, e11543 (2010).
Briffa, K. R. & Melvin, T. M. In Dendroclimatology. Developments in Paleoenvironmental Research, vol 11. (eds Malcolm, K. H., Henry, F. D. & Thomas, W. S.) 113–145, https://doi.org/10.1007/978-1-4020-5725-0_5 (Springle, Dordrechtr, 2011).
Brienen, R. J. W., Gloor, E. & Zuidema, P. A. Detecting evidence for CO2 fertilization from tree ring studies: The potential role of sampling biases. Global Biogeochem. Cycles 26 (2012).
Bowman, D. M. J. S., Brienen, R. J. W., Gloor, E., Phillips, O. L. & Prior, L. D. Detecting trends in tree growth: not so simple. Trends Plant Sci. 18, 11–7 (2013).
Nehrbass-Ahles, C. et al. The influence of sampling design on tree-ring-based quantification of forest growth. Glob. Chang. Biol. 20, 2867–85 (2014).
Brienen, R. J. W., Gloor, M. & Ziv, G. Tree demography dominates long-term growth trends inferred from tree rings. Glob. Chang. Biol. 23, 474–484 (2017).
Johnson, S. E. & Abrams, M. D. Age class, longevity and growth rate relationships: protracted growth increases in old trees in the eastern United States. Tree Physiol. 29, 1317–28 (2009).
Bigler, C. Trade-Offs between growth rate, tree size and lifespan of mountain pine (Pinus Montana) in the swiss national park. PLoS One 11, 1–18 (2016).
Di Filippo, A. et al. The longevity of broadleaf deciduous trees in Northern Hemisphere temperate forests: insights from tree-ring series. Front. Ecol. Evol. 3, 1–15 (2015).
Cook, E. R. & Kairiukstis, L. A. Methods of Dendrochronology: Applications in the Environmental Science. (Kluwer Academic Publishers, 1990).
Peters, R. L., Groenendijk, P., Vlam, M. & Zuidema, P. A. Detecting long-term growth trends using tree rings: A critical evaluation of methods. Glob. Chang. Biol. 21, 2040–2054 (2015).
Briffa, K. R. et al. Fennoscandian summers from ad 500: temperature changes on short and long timescales. Clim. Dyn. 7, 111–119 (1992).
Helama, S., Melvin, T. M. & Briffa, K. R. Regional curve standardization: State of the art. Holocene 27, 172–177 (2017).
Martínez-Vilalta, J., López, B. C., Adell, N., Badiella, L. & Ninyerola, M. Twentieth century increase of Scots pine radial growth in NE Spain shows strong climate interactions. Glob. Chang. Biol. 14, 2868–2881 (2008).
Voelker, S. L., Muzika, R.-M., Guyette, R. P. & Stambaugh, M. C. Historical CO2 growth enhancement declines with age in quercus and pinus. Ecol. Monogr. 76, 549–564 (2006).
Rolland, C., Petitcolas, V. & Michalet, R. Changes in radial tree growth for Picea abies, Larix decidua, Pinus cembra and Pinus uncinata near the alpine timberline since 1750. Trees 13, 40–53 (1998).
Barber, V. A., Juday, G. P. & Finney, B. P. Reduced growth of Alaskan white spruce in the twentieth century from temperature-induced drought stress. Nature 405, 668–73 (2000).
Andreu-Hayles, L. et al. Varying boreal forest response to Arctic environmental change at the Firth River, Alaska. Environ. Res. Lett. 6, 045503 (2011).
Sullivan, P. F., Pattison, R. R., Brownlee, A. H., Cahoon, S. M. P. & Hollingsworth, T. N. Effect of tree-ring detrending method on apparent growth trends of black and white spruce in interior Alaska. Environ. Res. Lett. 11, 114007 (2016).
Henry, J. D. & Swan, J. M. Reconstructing forest history from live and dead plant material–An approach to the study of forest succession in Southwest New Hampshire. Ecology 55, 772–783 (1974).
Lorimer, C. G. Age structure and disturbance history of a southern Appalachian virgin forest. Ecology 61, 1169–1184 (1980).
Gedalof, Z. & Berg, A. A. Tree ring evidence for limited direct CO2 fertilization of forests over the 20th century. Global Biogeochem. Cycles 24, 2–7 (2010).
Girardin, M. P., Guo, X. J., Bernier, P. Y., Raulier, F. & Gauthier, S. Changes in growth of pristine boreal North American forests from 1950 to 2005 driven by landscape demographics and species traits. Biogeosciences 9, 2523–2536 (2012).
Girardin, M. P. et al. Unusual forest growth decline in boreal North America covaries with the retreat of Arctic sea ice. Glob. Chang. Biol. 20, 851–866 (2014).
Hellmann, L. et al. Diverse growth trends and climate responses across Eurasia’s boreal. Environ. Res. Lett. 11, 074021 (2016).
Girardin, M. P. et al. Testing for a CO2 fertilization effect on growth of Canadian boreal forests. J. Geophys. Res. Biogeosciences 116, 1–16 (2011).
Nicault, A., Guiot, J., Edouard, J. L. & Brewer, S. Preserving long-term fluctuations in standardisation of tree-ring series by the adaptative regional growth curve (ARGC). Dendrochronologia 28, 1–12 (2010).
Frank, D., Esper, J., Zorita, E. & Wilson, R. A noodle, hockey stick, and spaghetti plate: A perspective on high-resolution paleoclimatology. Wiley Interdiscip. Rev. Clim. Chang. 1, 507–516 (2010).
Esper, J., Cook, E. R. & Schweingruber, F. H. Low-frequency signals in long tree-ring chronologies for reconstructing past temperature variability. Science 295, 2250–3 (2002).
Li, G., Harrison, S. P., Prentice, I. C. & Falster, D. Simulation of tree-ring widths with a model for primary production, carbon allocation, and growth. Biogeosciences 11, 6711–6724 (2014).
Girard, F., Payette, S. & Gagnon, R. Rapid expansion of lichen woodlands within the closed-crown boreal forest zone over the last 50 years caused by stand disturbances in eastern Canada. J. Biogeogr. 35, 529–537 (2008).
Duchesne, L., D’Orangeville, L., Ouimet, R., Houle, D. & Kneeshaw, D. Extracting coherent tree-ring climatic signals across spatial scales from extensive forest inventory data. PLoS One 12 (2017).
Ministère des Forêts de la Faune et des Parcs. Norme d’inventaire écoforestier, Placettes-échantillons temporaires, Édition 2016 (2016).
Ministère des Forêts de la Faune et des Parcs. Norme d’inventaire écoforestier, placettes-échantillons permanentes, édition 2016 (2016).
Stokes, M. A. & Smiley, T. L. An introduction to tree-ring dating. (University of Chicago Press, 1968).
The authors would like to thank the staff at the Direction des Inventaires Forestiers of the Ministère des Forêts, de la Faune et des Parcs du Québec for the work related to tree core sampling and processing, and for graciously sharing tree-ring chronologies and sample plot data from the forest inventory program in Quebec, Canada. We would also like to acknowledge Jean Noël for his assistance in spatial data processing and Denise Tousignant for English editing.
The authors declare no competing interests.
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