Water, Air, & Soil Pollution

, Volume 219, Issue 1–4, pp 43–57 | Cite as

Foliar Nitrogen Uptake from Wet Deposition and the Relation with Leaf Wettability and Water Storage Capacity

  • Sandy Adriaenssens
  • Jeroen Staelens
  • Karen Wuyts
  • An de Schrijver
  • Shari Van Wittenberghe
  • Tatiana Wuytack
  • Fatemeh Kardel
  • Kris Verheyen
  • Roeland Samson
  • Pascal Boeckx


This study assessed the foliar uptake of 15N-labelled nitrogen (N) originating from wet deposition along with leaf surface conditions, measured by wettability and water storage capacity. Foliar 15N uptake was measured on saplings of silver birch, European beech, pedunculate oak and Scots pine and the effect of nitrogen form (NH 4 + or NO 3 ), NH 4 + to NO 3 ratio and leaf phenology on this N uptake was assessed. Next to this, leaf wettability and water storage capacity were determined for each tree species and phenological stage, and the relationship with 15NH 4 + and 15NO 3 uptake was examined. Uptake rates were on average five times higher (p < 0.05) for NH 4 + than for NO 3 and four times higher for deciduous species than for Scots pine. Developing leaves showed lower uptake than fully developed and senescent leaves, but this effect was tree species dependent. The applied NH 4 + to NO 3 ratio did only affect the amount of N uptake by senescent leaves. The negative correlation between measured leaf contact angles and foliar N uptake demonstrates that the observed effects of tree species and phenological stage are related to differences in leaf wettability and not to water storage capacity.


Foliar uptake Nitrogen deposition Wettability Water storage capacity 15N labelling 

1 Introduction

During the last decades, human activities have dramatically increased atmospheric concentrations of reactive nitrogen (N) oxides (NOy) and ammonia (NH3) (Vitousek et al. 1997). Semi-natural ecosystems such as forests are exposed to higher inputs of these atmospheric pollutants compared with open-field circumstances because of their high surface roughness, leaf area index and physiological leaf characteristics (Erisman and Draaijers 2003). This increased N deposition to forest ecosystems has significantly altered internal N cycling and other forest ecosystem processes with potentially both beneficial and adverse consequences (Vitousek et al. 1997). Adverse consequences such as N saturation, soil acidification and shifts in biodiversity have widely been recognised (Aber et al. 1998; Gilliam 2006; Gundersen et al. 2006; Bowman et al. 2008), as well as the initial positive effect on tree and forest growth (Laubhann et al. 2009; Solberg et al. 2009; Thomas et al. 2010). However, the size and duration of the effect of enhanced N deposition on carbon (C) sequestration, still remains to be discussed (Nadelhoffer et al. 1999; Magnani et al. 2007; De Vries et al. 2009).

Atmospheric N can be taken up either by aboveground tree parts or by the forest soil (Rennenberg and Gessler 1999), two pathways which have shown to be interrelated (Bruckner et al. 1993; Rennenberg et al. 1998; Vallano and Sparks 2008). Nitrogen incorporated through foliage is a direct addition to metabolism, while N additions to the soil surface may also be incorporated into microbial biomass, revolatilized or leached (Rennenberg and Gessler 1999; Sparks 2009). Recent studies show that canopy N retention can amount to up to 70% of N deposition, providing as much as one third of tree N requirements without any competition from soil microbial biomass (Gaige et al. 2007; Sievering et al. 2007). However, other canopy elements than leaves, such as branches, boles and lichens can also provide a substantial sink for N through physico-chemical processes rather than by N assimilation (Dail et al. 2009). Next to this, Dail et al. (2009) showed that the vegetation and not the soil is the most important short-term sink under increased N availability. This retained N can be rapidly assimilated by the canopy (Calanni et al. 1999). Therefore, it is possible that canopy uptake will favour the growth response of historically N-limited forests (Sparks 2009).

Nitrogen uptake can occur via dry deposition (e.g. NH3 and NO2) and/or wet deposition (NH 4 + , NO 3 ) by foliage via stomata and the cuticle (Rennenberg and Gessler 1999). Generally, gaseous uptake of N compounds is driven by stomatal characteristics and can be modelled well using a compensation model developed by Sutton et al. (1998). In contrast, foliar uptake processes from wet deposition are stipulated by the surface conditions of the leaves, i.e. surface roughness and wax chemistry, which can be characterised by leaf wettability and water storage capacity (WSC) (Boyce et al. 1991). Since the uptake of dissolved ions is assumed to occur mainly via the cuticle (Peuke et al. 1998), higher wettability could favour this process by enlarging the contact area between incident rain droplets and the cuticle (Sase et al. 2008). Similarly, a higher WSC would prolong the contact period between incident rain and leaves and as such the time for exchange processes. These two parameters differ between tree species (Holloway 1969; Hall and Burke 1974) but also between different phenological stadia within one species (Sase et al. 2008). Moreover, they are easy to measure and could give clear indications about the expected foliar uptake for a range of different tree species and through the growing season.

An accurate quantification of canopy N uptake from wet deposition is frequently obtained by applying 15N-labelled sources at tracer levels. In contrast to throughfall measurements (Thimonier et al. 2005), it is possible with this technique to quantify direct foliar uptake and subsequent assimilation of N and to distinguish between N assimilated by living tissue or N adsorbed to canopy elements (Gaige et al. 2007; Dail et al. 2009). This 15N pulse chase technique has been used to investigate effects of tree species, N load and N form on foliar uptake, both in field studies (Brumme et al. 1992; Eilers et al. 1992; Lumme 1994; Boyce et al. 1996; Garten et al. 1998; Dail et al. 2009) and laboratory studies (Bowden et al. 1989; Garten and Hanson 1990; Lumme 1994; Lumme and Smolander 1996; Wilson and Tiley 1998; Chavez-Aguilar et al. 2006). However, most of these studies have used N loads far above ambient levels.

In this study, the15N pulse chase technique was used to quantify foliar N uptake from wet deposition under ambient N load levels for four ecologically different tree species. We hypothesise that foliar N uptake is influenced by tree species, N form, applied NH 4 + to NO 3 ratio and leaf phenological stage (the periods of leaf development, fully developed leaves and leaf senescence) and assessed the relative importance of these factors. Moreover, we test the hypothesis whether this N uptake is related to leaf wettability and leaf WSC.

2 Materials and Methods

2.1 Plant Material and Climate

This study was performed using living, leafed twigs of 3-year-old potted saplings of European beech (Fagus sylvatica L.), pedunculate oak (Quercus robur L.), silver birch (Betula pendula Roth) and Scots pine (Pinus sylvestris L.). These species are widespread in temperate regions but have a different ecological behaviour (i.e. pioneer vs climax species, deciduous vs coniferous species and sun leaves vs shade leaves) (Fitter and Peat 1994; and a different canopy structure (i.e. leaves vs needles), which may have an influence on foliar nitrogen uptake. All saplings were grown in a tree nursery and were of known provenance. They were potted on 27th February 2008 in a mixture of peat and slow releasing fertiliser (8.6 g N kg−1 dry soil year−1) in order to eliminate the effect of varying soil nutrient availability on aboveground N uptake by leaves. The saplings were placed at a wind sheltered location in the close vicinity of the laboratory near Ghent (north of Belgium, approximately 60 km from the North Sea in the prevailing wind direction; 50°58 N, 3°49 E). Mean annual precipitation (1980–2008) at a nearby weather station operated by the Belgian Royal Meteorological Institute ( is 784 mm and is distributed equally over the year, and mean annual temperature is 10.4°C. The region of Flanders is characterised by relatively high atmospheric N and sulphur (S) deposition. In the period 2002–2006, average annual total deposition fluxes to a mixed beech forest nearby amounted to 30 kg N ha−1 year−1 and 20 kg S ha−1 year−1 (Verstraeten et al. 2007).

2.2 Experimental Setup and Sample Analysis

2.2.1 15N Application

Two twigs with a length of approximately 30 cm were selected per tree (four replicated trees per treatment) and were sprayed with an artificial rainwater solution of inorganic salts in deionised water. It contained all major ions, with concentrations (in mg L−1) based on average precipitation data for this area in 2002–2006 (VMM 2007): 0.82 (Na+), 0.09 (K+), 0.44 (Ca2+), 0.17 (Mg2+), 0.67 (SO 4 2− -S) and 2.07 (Cl). The pH amounted to 5.5. One twig was sprayed with a solution containing 15N-labelled (99 at.%) NH 4 + ; the other was sprayed with 15N-labelled (99 at.%) NO 3 . Two types of solutions were applied as separate treatments, subsequently called the ‘high NH 4 + to NO 3 ratio’ and the ‘low NH 4 + to NO 3 ratio’ treatments. The concentration of NH 4 + –N was similar in both solutions (0.84 mg L−1). However, in the low NH 4 + to NO 3 ratio treatments, the concentration of NO 3 -N (1.26 mg L−1) and Cl (5.00 mg L−1) were three and 2.42 times higher than those in the high NH 4 + to NO 3 ratio treatments (0.42 mg NO 3 –N L−1 and 2.07 mg Cl L−1). As such, the NH 4 + to NO 3 ratio differed by a factor of three between the treatments (2:3 versus 2:1), hereby simulating increased future emissions of reactive N compounds by combustion processes.

A preliminary test revealed that the 15N enrichment in sprayed leaves was similar 2 and 24 h after 15N application. Therefore, branches were removed 2 h after the first application to ensure complete N uptake from plant surfaces while preventing meaningful transport of 15N containing assimilation products to other tree parts. Each twig was sprayed two times with 100 ml of the rainwater solution with a 1-h interval to allow leaves to dry, and was cut 1 h after the second application. The volume sprayed was sufficient to start drainage from the twigs. All equipment was used in duplicate to avoid any cross-contamination between 15NH 4 + and 15NO 3 treatments. The living twigs were sprayed in boxes to prevent 15N contamination of other plant parts. To quantify the exact amount of solution applied to each twig, the initial and final weights of the sprayer were registered. The experiment was conducted on developing leaves (15 May 2008 for birch and pine and 28 May 2008 for beech and oak), fully developed leaves (19 Aug 2008 for all species) and senescent leaves (19 Sept 2008 for birch and pine and 16 Oct 2008 for beech and oak) to assess the effect of leaf phenology on N uptake. The spring and autumn experiments were done earlier for birch and pine than for beech and oak to account for the different phenology of the species. Since needle sprouting of pine occurred late in the growing season (June), no results are available for the developing stage of pine.

2.2.2 Measurement of Leaf Wettability and Visualisation of Leaf Surface Structure

Contact angles (CAs) of standardised water droplets with the leaf surface can be used as a proxy for leaf wettability (Brewer et al. 1991). Low angles indicate the tendency to form water films rather than droplets, high angles indicate water repellence. The CAs were measured, using the software ImageJ, from digital photographs of a water droplet (7 μl for the deciduous species; 3 μl for Scots pine) on the abaxial and adaxial leaf surfaces of non-treated branches (Canon EOS 5D digital camera and Sigma macro lens EX DG 105 mm, f 2.8). Ten replicates per species, phenological stage and leaf side were measured.

Next to this, the leaf surface structure was visualised by digital photographs at different magnifications. Firstly, four samples of fresh leaf material of all species were taken and kept in a 70% ethanol solution. Later, they were mounted on aluminium stubs using a double-sided adhesive tape and immediately dried in a critical point dryer (Balzers CPD-010 unit). Afterwards, they were sputtered with gold (30–40 nm thick) using a sputter coater (Cressington 108 auto) and transferred to the cold stage of a scanning electron microscope (Philips 515 SEM) by means of a transfer rod under high vacuum, after opening the transfer valve with an acceleration voltage of 20 kV.

2.2.3 Estimation of Leaf/Needle Biomass, Water Storage Capacity and Surface Area

Before 15N application, a representative twig of each tree was sampled to measure leaf biomass, WSC and surface area. The WSC of leaves, defined as the difference between the wetted and dry biomass divided by leaf area, was determined to estimate interception during a normal rain event. In contrast to leaf wettability, WSC is also influenced by leaf orientation and could render a more realistic measurement under ambient conditions. For this purpose, a laboratory experiment adapted from Aston (1979) and Herwitz (1985) was conducted. The representative twig was severed at its base only seconds before the experiment in order to prevent wilting. Next, each twig was suspended in turn from a balance (precision of 0.001 g) at an angle to the vertical approximately the same as its former angle to the stem. The weight of the branch was then recorded under the following conditions: (a) non-wetted (fresh weight), (b) fully wetted by continuous spraying with a garden sprayer and (c) after dripping. Next, the leaves were removed from the twigs and the experiment was repeated. The WSC was calculated for fully wetted leaves and after dripping, representing respectively calm and windy conditions, as the difference between the WSC of fully leafed branches and the WSC of twigs only. After the experiment, the remaining detained water was allowed to evaporate, the leaves and branches were separated and the surface area was measured. Total one-sided leaf area of the deciduous species was measured with a LI-3000 Portable Area Meter (LICOR, Lincoln, Nebraska). Needle surface area was estimated assuming a half cylindrical shape and based on the number of needles per branch and the mean needle length and diameter of ten randomly selected needles.

2.2.4 Analysis of Plant Material

After harvesting, all twigs were washed thoroughly with deionised water in order to remove any 15N adsorbed to the surface of leaves/needles or branches. Next, leaves, needles and branches were separated, dried in paper bags for 48 h at 50°C, weighed and ground to a fine powder (<250 μm) using a centrifugal mill (Retsch ZM1, Germany). Finally, samples were analysed for total N and 15N in duplicate using an elemental analyzer (EA) interfaced to an isotope ratio mass spectrometer (IRMS) (20–20, SerCon, UK). Machine error (n = 10) of this EA-IRMS system is 0.2‰ for δ15N. Cross-contamination was avoided by including method blanks and analytical quality was checked by the standard deviation of two replicate measurements.

2.2.5 Analysis of Plant Available Inorganic Nitrogen

From April to October 2008, soil was sampled monthly from three different control pots (without a tree) and frozen immediately. Plant available soil NH 4 + was determined colorimetrically in a KCl extract (1 M, soil:solution ratio 1:2, 1 h) by the salycilate-nitroprusside method on an auto-analyzer (AA3, Bran and Luebbe, Germany). Nitrate was determined colorimetrically (AA3) after reduction in a Cu–Cd column followed by reaction of nitrite with N-1-napthylethylenediamine to produce a chromophore.

2.3 Data Processing

Uptake of 15N per unit dry plant material (μg N g−1 DM) was calculated by accounting for the natural abundance of 15N in untreated branches (Harrison et al. 2000):
$$ Y = X \cdot \frac{{{\text{at}}{ }{\%_{\rm{treated}}} - {\text{at}}{ }{\%_{\rm{untreated}}}}}{{{\hbox{at}}{ }{\%_{\rm{solution}}} - {\hbox{at}}{ }{\%_{\rm{untreated}}}}} \cdot {10^3} $$
with Y being the 15N uptake (μg g−1 DM) and X is the total N concentration (mg g−1 DM) in the treated samples.

Calculated N uptake for each combination of tree species, NH 4 + to NO 3 ratio, N form and leaf phenological stage was tested for significant difference from zero by means of a one sample t test. ANOVA on the measured 15N uptake was not possible due to heteroscedasticity across tree species, leaf phenology, N form and NH 4 + to NO 3 ratio according to Levene’s equality of variance test. However, by splitting up the data according to the N form, three-way ANOVA allowed us to assess the effect of the remaining factors on 15N uptake. Three-factor interaction was excluded from the model because of insufficient degrees of freedom. Means were separated by Tukey’s honestly significant difference test and p values were calculated for each factor. Afterwards, data were split up according to tree species, leaf phenology and NH 4 + to NO 3 ratio to assess two-factor interactions. Data of WSC and 15N uptake were log-transformed to meet normality conditions. The effect of N form was then tested by means of two-tailed t tests per tree species, NH 4 + to NO 3 ratio and phenological stage. For pine, an additional univariate analysis was done including needle age as extra factor. Differences in WSC for fully wetted leaves and for leaves after dripping and CA on the abaxial and adaxial side were tested by analysis of variance (ANOVA) with tree species and phenological stage as factors. Correlations between WSC, CA, foliar N content and 15NH 4 + and 15NO 3 uptake were assessed by calculating Spearman’s rank coefficients. All statistical analyses were performed using SPPS 15.0 with a minimum significance level of p < 0.05.

3 Results

3.1 Foliar N Uptake

The foliar uptake of 15NH 4 + ranged from 0.70 μg g−1 DM for pine to 3.76 μg g−1 DM for birch, while the uptake of 15NO 3 varied between 0.11 μg g−1 for pine and 0.86 μg g−1 DM for birch. This uptake was significantly higher than zero in most cases (Table 1). Generally, the uptake of 15NH 4 + was significantly higher than the uptake of 15NO 3 , except for the fully developed needles of pine under both the low and high NH 4 + to NO 3 ratio and senescent birch and developing beech leaves under high NH 4 + to NO 3 ratio. On average, the uptake of NH 4 + was approximately seven and three times higher than the uptake of NO 3 in the high (2:1) and low (2:3) NH 4 + to NO 3 ratios, respectively, but varied with tree species and phenological stage.
Table 1

Mean 15N–NH 4 + and 15N–NO 3 uptake (μg g−1 DM) by the leaves of four tree species in three-leaf phenological stages after applying artificial rainwater with high (2:1) or low (2:3) NH 4 + to NO 3 ratio

Tree species

Leaf phenology

High NH 4 + to NO 3 ratio

Low NH 4 + to NO 3 ratio

15N–NH 4 +

15N–NO 3

15N–NH 4 +

15N–NO 3

Silver birch






Fully developed










European beech






Fully developed










Pedunculate oak






Fully developed










Scots pine






Fully developed










Negative values indicate higher 15N values in control samples than in treated samples. Different small letters within a row indicate significant (p < 0.05) differences between NH 4 + and NO 3 uptake for a specific tree species, phenological stage and NH 4 + to NO 3 ratio

*p < 0.05, N uptake is significantly different from zero

**Only last year’s needles

According to the univariate analysis, both the 15NH 4 + and 15NO 3 uptake were significantly influenced, in decreasing order of importance, by tree species, leaf phenology and NH 4 + to NO 3 ratio and by the two-factor interactions of these three factors (Table 2). Under both the high and low NH 4 + to NO 3 ratio, the tree species effect on 15NH 4 + uptake was pronounced by a higher uptake for deciduous species versus pine (Table 1). For 15NO 3 , the uptake was significantly larger for birch and beech than for oak and pine. In general, 15NH 4 + uptake was significantly higher for senescent leaves than for developing and fully developed leaves (p < 0.0001), but this effect was species dependent. For example, in the leaf developing stage birch showed the highest uptake rates while beech, oak and pine showed the lowest uptake rates. Nitrate uptake of all species was significantly lower for developing leaves compared with fully developed and senescent leaves. The effect of NH 4 + to NO 3 ratio is largely manifested on senescent leaves which showed a lower 15NH 4 + uptake and a higher 15NO 3 uptake under the low NH 4 + to NO 3 ratio.
Table 2

Degrees of freedom (df) and F and p values of a three-way ANOVA: effect of tree species, leaf phenology and NH 4 + to NO 3 ratio on the observed foliar 15N uptake of NH 4 + and NO 3

Source of variation

15NH 4 + uptake

15NO 3 uptake







Tree species







Leaf phenology







NH 4 + to NO 3 ratio







Tree species × leaf phenology







Tree species × NH 4 + to NO 3 ratio







Leaf phenology × NH 4 + to NO 3 ratio







*p < 0.05, significant

Univariate analysis of variance for pine reveals a significant effect of needle age on the observed 15NO 3 uptake (p = 0.029). The higher 15NO 3 uptake by current year needles compared with last year needles was only visible during summer (Fig. 1). For the developing stage, however, no comparison could be made. Ammonium uptake was not found to be affected by needle age, which was probably due to the relatively large standard deviation of the 15NH 4 + uptake. The effect of leaf phenology and the NH 4 + to NO 3 ratio was significant for both the 15NH 4 + and NO 3 uptake of current and last year needles and similar to the effects described in the univariate analysis for all species.
Fig. 1

15N uptake (μg g−1 DM) (±standard deviation) by current and last year needles of Scots pine per phenological stage

3.2 Leaf Characteristics

The foliar N content of the deciduous tree species decreased from spring (3.91%) to autumn (2.62%) whereas for current year and last year needles of pine foliar N increased slightly from 1.36% to 1.58% (Fig. 2).
Fig. 2

Total N content (%) of birch, beech and oak leaves and pine needles in the different phenological stages and KCl-extractable soil NH 4 + and NO 3 content (mg N kg−1 dry soil) in the control pots through the growing season of 2008

The CA of droplets (Table 3) on the abaxial side of leaves was significantly lower for birch than for the other species, while the highest CA was observed for oak, although differences were not significant for all species. At the adaxial side, birch also showed the lowest CA, but differences between species were less significant. Pine showed the highest adaxial CA in the stages with fully developed and senescent leaves. At the abaxial side, CA of oak and pine was lower at the developing stage than at the later stages. The same pattern was observed at the adaxial side for pine, but for birch and oak, a lower CA and thus higher wettability can be seen towards the end of the growing season (at senescence) and, for beech, at the stage of fully developed leaves.
Table 3

Contact angle (CA; °) of water droplets on the adaxial and abaxial leaf side and water storage capacity (WSC; g m−2) of fully wetted leaves and leaves after dripping per phenological stage and tree species

Leaf phenology

Tree species

CA adaxial side

CA abaxial side

WSC fully wetted

WSC after dripping


Silver birch





European beech





Pedunculate oak





Scots pine*




Fully developed

Silver birch





European beech





Pedunculate oak





Scots pine






Silver birch





European beech





Pedunculate oak





Scots pine





Small letters within a column indicate significant (p < 0.05) differences between tree species in a specific phenological stage; capital letters indicate significant (p < 0.05) differences between phenological stages for a specific tree species

*Only last year’s needles

Birch and beech show a smooth leaf surface structure, both on the adaxial and on the abaxial side, with no outgrowing hairs or trichomes visible (Fig. 3). In contrast, oak leaves have distinct crystalline epicuticular wax structures on the abaxial side, which also cover the stomatal guard cells and trichomes. On the adaxial side, the same crystalline wax structures are visible, but less abundant. Pines have a sinuate needle surface structure orientated perpendicular to the length axis of the needles, along which the stomata are situated. Pine stomata are raised above the surface, which is covered with a wax layer that has some crystalline structures.
Fig. 3

Scanning electron microscope images taken from the (a) abaxial and (bc) adaxial leaf side of respectively (1) birch (×1,200;×4,780), (2) beech (×2,620;×2,720;×10,900), (3) oak (×2,500;×1,010;×9,600) and (4) pine (×2,500;×625;×8,400)

The WSC of fully wetted leaves and WSC after dripping differed significantly between tree species, but the ranking depends on the phenological stage (Table 3). Nonetheless, at each phenological stage, we observed the lowest WSC values for pine or birch and the highest for beech or oak. WSC for fully wetted leaves and WSC after dripping were significantly correlated (correlation coefficient = 0.72), with the highest difference between both values for oak.

Relating the CA data of the adaxial leaf side to the N uptake rates found in this experiment yielded a correlation coefficient of −0.70 for 15NH 4 + (p = 0.019) and −0.73 for 15NO 3 (p = 0.011) (Fig. 4). Next to this, 15NH 4 + uptake was positively correlated to the foliar N content (p < 0.0001; r = 0.391). However, on a species basis, we found a negative relationship between 15NH 4 + uptake and foliar N content for beech (p < 0.001; r =−0.72) and oak (p = 0.048; r =−0.407) and no significant relation (p > 0.05; r < 0.418) for birch and pine. The CA of the abaxial leaf side and WCS after dripping were not significantly correlated with 15NH 4 + or 15NO 3 uptake (p > 0.05; r < 0.57).
Fig. 4

Relation between the leaf contact angles (°) measured at the adaxial leaf side and the 15NH 4 + (p = 0.019; r =−0.70) and 15NO 3 uptake (p = 0.011; r =−0.73; μg g−1 DM)

Plant available inorganic N in the control pots decreased through the growing season (Fig. 2). The NH 4 + availability, in particular, decreased from April (456 mg N kg−1 soil) towards October, to the same level as the NO 3 availability (±120 mg N kg−1 soil).

4 Discussion

4.1 Effect of N Form

In our study, NH 4 + was more readily taken up than NO 3 , even when the NO 3 concentration in the solution was higher than that of NH 4 + . One reason may be that the transport of NO 3 and NH 4 + primarily occurs through cuticular diffusion (Peuke et al. 1998). Cations are transported much more readily through cuticles than anions because of the presence of hydrophilic pores within the cuticle. These small pores are lined with fixed negative charges (presumably mainly from polygalacturonic acids), with increasing density from the outside of the cuticle to the inside. Accordingly, permeation of cations along this gradient is enhanced whereas anions are repulsed from this region (Tyree et al. 1990). There is also evidence of a stomatal pathway for the uptake of polar and ionic solutes, which is located at the surface of the stomatal pores and is not affected at all by the charge of the N compound entering (Eichert and Goldbach 2008). However, the importance of this stomatal pathway is low in comparison with the cuticular uptake pathway.

The preferential N uptake of NH 4 + compared with NO 3 is consistent with previous studies for both deciduous (Garten and Hanson 1990; Brumme et al. 1992) and coniferous trees (Bowden et al. 1989; Eilers et al. 1992; Lumme 1994; Boyce et al. 1996; Lumme and Smolander 1996; Wilson and Tiley 1998). The ratio of 15NH 4 + uptake to 15NO 3 uptake varied from 7.9 for pine under the high NH 4 + to NO 3 ratio treatment to 3.0 for oak under the low NH 4 + to NO 3 ratio treatment, which is concordant with most of these literature data (Bowden et al. 1989; Garten and Hanson 1990; Eilers et al. 1992; Boyce et al. 1996; Lumme and Smolander 1996; Wilson and Tiley 1998), but not with all (Garten and Hanson 1990; Brumme et al. 1992; Dail et al. 2009). All these studies applied a NH 4 + to NO 3 ratio of one.

Significant uptake of both NH 4 + and NO 3 occurs through leaves when rainwater is passing the canopy, and this uptake should be accounted for when calculating canopy uptake from throughfall measurements. It is also clear from this experiment that the proposed efficiency factor by de Vries et al. (2001) of NH 4 + vs NO 3 uptake with a value of 6 is not applicable for all tree species and throughout the year. In addition, it is necessary to account for retention by branches and boles as well (Dail et al. 2009) and for dry deposition processes to determine the value of this efficiency factor.

4.2 Tree Species Effect

Next to the analogous studies of Brumme et al. (1992) and Eilers et al. (1992) with European beech and Norway spruce, respectively, to our knowledge the present report is the only experimental comparison of foliar 15N uptake by deciduous and coniferous species under similar conditions. We found that the mean NH 4 + uptake rates of silver birch, European beech and oak were respectively six, three and four times higher than for pine. For NO 3 uptake, this ratio was respectively six, three and three. Brumme et al. (1992) found that NH 4 + uptake by beech leaves was 1.8 times higher than spruce needles, and NO 3 uptake 2.7 times. In that experiment, however, the applied N concentration was much higher than ambient levels, which could explain the different result.

Several explanations can be put forward for the observed tree species effect on N uptake. Firstly, the tree species showed significant differences in wettability, which relates to N uptake (see section 4.5), with higher wettability for birch and lower for pine. Secondly, although of less importance, broadleaf trees are found to differ in internal resistance for NO 3 compared with conifers (Ammann et al. 1999). Thirdly, the N demand of coniferous tree species is thought to be relatively low, owing to lengthy needle retention, efficient internal N recycling and the ability of these species to produce large amounts of aboveground biomass per unit N assimilated (Dail et al. 2009). The latter is supported by the N content in the pine needles (1.4%), which is less than half of that in the leaves of the three deciduous species (3.2%) (Fig. 3). Fourthly, the cuticular pore density (see section 4.1) is higher in cell walls between guard cells of stomata and subsidiary cells (Maier-Maercker 1983). Positive relationships between the number or distribution of stomata and the intensity of mineral nutrient uptake from foliar sprays have been observed (Levy and Horesh 1984).

Despite this large difference in uptake rates, it is likely that the annual foliar N uptake of pine will be higher than for the deciduous species, considering the presence of needles throughout the year compared with only 6 months for deciduous species. Extrapolating the average results of the high NH 4 + to NO 3 ratio treatment from one branch to mature stands with a LAI of 1.4 for silver birch (Wuyts et al. 2008), 5.5 for beech (Mussche et al. 2001), 2.4 for oak and 2.9 for pine (Sampson et al. 2006) results in an annual foliar uptake of 0.08, 0.43, 0.24 and 2.23 kg N ha−1, respectively, from wet deposition under ambient levels. Leaf surface area of the treated branches, was calculated from their leaf biomass and the specific leaf area of the control branches, which was respectively 203, 302, 239 and 369 cm2 g−1 DM for birch, beech, oak and pine. Considering a wet N deposition of 10 kg−1 N ha−1 year−1 (N level as in the high NH 4 + to NO 3 ratio and a mean annual precipitation of 791 mm), the fraction of N taken up by foliage from wet deposition would equal 0.8% for birch, 4.3% for beech, 2.4% for pedunculate oak and 22.3% for pine. These annual uptake values suggest that the contribution of foliar uptake from wet deposition by deciduous species is of minor importance in the total canopy N uptake of 4–5 kg N ha−1 year−1 calculated from throughfall measurements (Thimonier et al. 2005; Staelens et al. 2008). However, on a canopy level, it is also important to consider the role of woody plant surfaces (see section 4.1), since these have been shown to contribute significantly to the total water storage capacity (Herwitz 1985; Andre et al. 2008), and the effect of varying rain intensity (Hansen et al. 1994).

4.3 Effect of Leaf Phenology

Generally, the highest uptake rates were observed for fully developed and senescent leaves. This is in line with observations from throughfall studies for both coniferous (Houle et al. 1999) and deciduous stands (Neary and Gizyn 1994; Houle et al. 1999). One reason that N uptake occurs at leaf senescence, is that it is probably linked to N retranslocation by trees (Houle et al. 1999; Hagen-Thorn et al. 2006). Species with early leaf fall seem to resorb nutrients at a higher rate, thereby exhibiting a trade-off between early leaf fall and efficient nutrient resorption (Niinemets and Tamm 2005). This also held true in the present study, where the N content of birch decreased by 17% from fully developed leaves towards senescent leaves whereas for beech and oak this was 16% and 13%, respectively.

However, there are some arguments that indicate that plant N status may not be the only driving factor for foliar N uptake. Firstly, for both the current and last year needles of pine a higher 15NH 4 + uptake was observed in the senescence stage, which was not coupled with a decrease in needle N content. Current year needles are fully developed at the end of the growing season, and, as indicated by studies on other evergreen species, will serve as main N storage site during winter (Millard and Proe 1993), which can explain their higher uptake. For last year needles no clear mechanism can be put forward. Secondly, beech and oak showed an increased 15NH 4 + uptake with decreasing N content, with the lowest uptake rates occurring during leaf emergence, whereas birch and pine did not show this pattern. The difference during leaf emergence could be due to the higher photosynthetic capacity of the sunlit leaves/needles of birch and pine compared with the shadow leaves of beech and oak (Hikosaka 2005). It is also possible that the higher N availability in the pots during leaf emergence had an influence the foliar N uptake, although it has been shown that leaf growth in spring is largely determined by the N stored in plant tissue during the previous year (Millard and Thompson 1989). So, although plant N status can partly explain the differences between the different phenological stadia, there is an interaction with leaf wettability and species-specific photosynthetic capacity.

4.4 Effect of NH 4 + to NO 3 Ratio

In the present study, no distinct effect of the applied NH 4 + to NO 3 ratio was found, except for senescent leaves, in contrast to previous reports for European beech (Brumme et al. 1992), sacred fir (Abies religiosa) (Chavez-Aguilar et al. 2006) and Norway spruce (Eilers et al. 1992; Lumme and Smolander 1996). In the experiments of Eilers et al. (1992) and Brumme et al. (1992), however, the low and high dose differed by a factor of seven, compared with the factor of three used in this experiment. In the other studies mentioned, NH 4 + and NO 3 were applied separately, thereby not accounting for preferential uptake.

The absence of a clear effect of the applied NO 3 concentration on the measured 15N uptake, and consequently of the NH 4 + to NO 3 ratio, indicates that the affinity of leaves and needles for NH 4 + is much higher than for NO 3 (see section 4.1), and that the ratios of NH 4 + to NO 3 used in this experiment are not sufficient to counter this balance. This implies that the potentially increasing future NO2 emissions in industrialised regions (Carslaw et al. 2007) with simultaneously decreasing NH3 emissions (Monks et al. 2009) will result in higher N deposition fluxes to the forest floor. So, although total N emissions may decrease in the near future, ecosystems will still be subject to N saturation and enhanced soil acidification and consequent changes in vitality and biodiversity.

4.5 Leaf Surface Characteristics and N Uptake

Leaf wettability is species dependent, since the physico-chemical characteristics of the epicuticular wax deposit and epidermal cell morphology differ between species (Holloway 1969; Hall and Burke 1974; Haines et al. 1985). Therefore, the SEM images (Fig. 3) partly explain the observed differences in wettability through visible differences in surface structure: the smooth surface of birch and beech causes water droplets to spread, while the crystalline epicuticular wax structures for oak and pine retain droplets as a sphere. Although the WSC of leaves is also generally indicative of wettability, we found no relationship between the CA and laboratory estimates of WSC after dripping, which is in contrast to the negative relationship observed by Haines et al. (1985). We hypothesise that this lack of relation can be attributed to the use of other tree species in this study and the difference in leaf orientation of the deciduous species. Birch leaves have a lower WSC than oak leaves because they tend to hang down vertically compared with the horizontally orientated oak leaves, which causes water to drip off faster. The vertical orientation of pine needles causes WSC to be low. With regard to the foliar N uptake, adaxial leaf wettability appears to be a more determinant factor than WSC. This could be explained by the fact that permeability through cuticular pores increases with leaf surface humidity. Therefore, a higher leaf surface covered by water, as in the case of low CAs, causes a higher permeability for inorganic ions (Schreiber et al. 2001). The WSC is a static parameter, measuring only the water amount that remains on the leaf surface after a rain event, while during this event more water makes contact with a leaf but then drips off. This suggests that the process of leaf N uptake occurs very fast, since the WSC, and as such the contact time, is less for birch than for oak leaves though N uptake is higher for birch than for oak.

To our knowledge, this is the first study relating foliar uptake of N originating from wet deposition to leaf surface properties. Our finding is concordant with the work of Sase et al. (2008) indicating a positive correlation between the net fluxes of NH 4 + and NO 3 from throughfall water and the leaf CA for Japanese cedar through the growing season. In their case, however, N uptake may have occurred through wet and dry deposition. It should be mentioned that possibly a similar pattern exists for dissolved N uptake by branches, which remains to be investigated. Also, within one species, leaf wettability can vary according to canopy height (Boyce et al. 1991) and stand characteristics (Hall et al. 1965) as an adaption to different microclimatic conditions such as light availability and relative humidity, and to the degree of leaf surface contamination (Barthlott and Neinhuis 1997). Since in this study the relation between N uptake and wettability was only observed for saplings growing in the same climatic conditions, it is important to further assess this relation within one species under varying conditions.

5 Conclusions

This study demonstrates that N assimilation of wet deposited NH 4 + and NO 3 occurs through foliage of deciduous and coniferous trees and that it is significantly influenced by N form, tree species, leaf phenology and NH 4 + to NO 3 ratio. Uptake of NH 4 + and NO 3 is strongly related to leaf wettability, and not to water storage capacity, a relationship which enables the indirect estimation of N uptake from this easy to measure parameter. However, there is still not much known about within-species dependence of N uptake on leaf wettability. In this study, the N uptake was small, so, it should be further examined to what extent N uptake from wet deposition contributes to total canopy N uptake. Furthermore, more research is needed to understand how this N uptake is related to throughfall deposition as easy and inexpensive technique for assessing total deposition fluxes.



We gratefully acknowledge L. Willems, G. De bruyn, K. Van Nieuland, J. Vermeulen, K. Ceunen and A. De Mey for field and laboratory assistance. The first and sixth authors are granted a Ph.D. fellowship by the Research Foundation—Flanders (FWO) and the Institute for the Promotion of Innovation through Science and Technology in Flanders (IWT-Vlaanderen), respectively. The second and fourth authors are funded as postdoctoral fellows of FWO and the third author as postdoctoral fellow of the Special Research Fund of Ghent University (BOF). The seventh author is funded by the Flemish institute for support of Scientific-Technologic Research in Industry.


  1. Aber, J., McDowell, W., Nadelhoffer, K., Magill, A., Berntson, G., Kamakea, M., et al. (1998). Nitrogen saturation in temperate forest ecosystems—hypotheses revisited. Bioscience, 48, 921–934.CrossRefGoogle Scholar
  2. Ammann, M., Siegwolf, R., Pichlmayer, F., Suter, M., Saurer, M., & Brunold, C. (1999). Estimating the uptake of traffic-derived NO2 from N-15 abundance in Norway spruce needles. Oecologia, 118, 124–131.CrossRefGoogle Scholar
  3. Andre, F., Jonard, M., & Ponette, Q. (2008). Precipitation water storage capacity in a temperate mixed oak-beech canopy. Hydrological Processes, 22, 4130–4141.CrossRefGoogle Scholar
  4. Aston, A. R. (1979). Rainfall interception by 8 small trees. Journal of Hydrology, 42, 383–396.CrossRefGoogle Scholar
  5. Barthlott, W., & Neinhuis, C. (1997). Purity of the sacred lotus, or escape from contamination in biological surfaces. Planta, 202, 1–8.CrossRefGoogle Scholar
  6. Bowden, R. D., Geballe, G. T., & Bowden, W. B. (1989). Foliar uptake of N-15 from simulated cloud water by red spruce (Picea-Rubens) seedlings. Canadian Journal of Forest Research-Revue Canadienne De Recherche Forestiere, 19, 382–386.CrossRefGoogle Scholar
  7. Bowman, W. D., Cleveland, C. C., Halada, L., Hresko, J., & Baron, J. S. (2008). Negative impact of nitrogen deposition on soil buffering capacity. Nature Geoscience, 1, 767–770.CrossRefGoogle Scholar
  8. Boyce, R. L., Mccune, D. C., & Berlyn, G. P. (1991). A comparison of foliar wettability of red spruce and balsam fir growing at high elevation. The New Phytologist, 117, 543–555.CrossRefGoogle Scholar
  9. Boyce, R. L., Friedland, A. J., Chamberlain, C. P., & Poulson, S. R. (1996). Direct canopy nitrogen uptake from N-15-labeled wet deposition by mature red spruce. Canadian Journal of Forest Research-Revue Canadienne De Recherche Forestiere, 26, 1539–1547.CrossRefGoogle Scholar
  10. Brewer, C. A., Smith, W. K., & Vogelmann, T. C. (1991). Functional interaction between leaf trichomes, leaf wettability and the optical properties of water droplets. Plant, Cell & Environment, 14, 955–962.CrossRefGoogle Scholar
  11. Bruckner, G., Gebauer, G., & Schulze, E. D. (1993). Uptake of (NH3)-N-15 by Picea abies in closed-chamber experiments. Isotopenpraxis, 29, 71–76.CrossRefGoogle Scholar
  12. Brumme, R., Leimcke, U., & Matzner, E. (1992). Interception and uptake of NH4+ and NO3 from wet deposition by aboveground parts of young beech (Fagus sylvatica L) trees. Plant and Soil, 142, 273–279.CrossRefGoogle Scholar
  13. Calanni, J., Berg, E., Wood, M., Mangis, D., Boyce, R., Weathers, W., et al. (1999). Atmospheric nitrogen deposition at a conifer forest: response of free amino acids in Engelmann spruce needles. Environmental Pollution, 105, 79–89.CrossRefGoogle Scholar
  14. Carslaw, D. C., Beevers, S. D., & Bell, M. C. (2007). Risks of exceeding the hourly EU limit value for nitrogen dioxide resulting from increased road transport emissions of primary nitrogen dioxide. Atmospheric Environment, 41, 2073–2082.CrossRefGoogle Scholar
  15. Chavez-Aguilar, G., Fenn, M. E., Gomez-Guerrero, A., Vargas-Hernandez, J., & Horwath, W. R. (2006). Foliar nitrogen uptake from simulated wet deposition in current-year foliage of Abies religiosa (H. B. K.) Schl. et Cham. Agrociencia, 40, 373–381.Google Scholar
  16. Dail, D. B., Hollinger, D. Y., Davidson, E. A., Fernandez, I., Sievering, H. C., Scott, N. A., et al. (2009). Distribution of nitrogen-15 tracers applied to the canopy of a mature spruce-hemlock stand, Howland, Maine, USA. Oecologia, 160, 589–599.CrossRefGoogle Scholar
  17. de Vries, W., Reinds, G.J., van der Salm, C., Draaijers, G., Bleeker, A. & Erisman, J.W. (2001). Intensive monitoring of forest ecosystems in Europe. Technical report 2001. Brussels, Geneva: EC-UN/ECE.Google Scholar
  18. de Vries, W., Solberg, S., Dobbertin, M., Sterba, H., Laubhann, D., van Oijen, et al. (2009). The impact of nitrogen deposition on carbon sequestration by European forests and heathlands. Forest Ecology and Management, 258, 1814–1823.CrossRefGoogle Scholar
  19. Eichert, T., & Goldbach, H. E. (2008). Equivalent pore radii of hydrophilic foliar uptake routes in stomatous and astomatous leaf surfaces—further evidence for a stomatal pathway. Physiologia Plantarum, 132, 491–502.CrossRefGoogle Scholar
  20. Eilers, G., Brumme, R., & Matzner, E. (1992). Aboveground N-uptake from wet deposition by Norway spruce (Picea-abies Karst). Forest Ecology and Management, 51, 239–249.CrossRefGoogle Scholar
  21. Erisman, J. W., & Draaijers, G. (2003). Deposition to forests in Europe: most important factors influencing dry deposition and models used for generalisation. Environmental Pollution, 124, 379–388.CrossRefGoogle Scholar
  22. Fitter, A. H., & Peat, H. J. (1994). The ecological flora database. Journal of Ecology, 82, 415–425.CrossRefGoogle Scholar
  23. Gaige, E., Dail, D. B., Hollinger, D. Y., Davidson, E. A., Fernandez, I. J., Sievering, H., et al. (2007). Changes in canopy processes following whole-forest canopy nitrogen fertilization of a mature spruce-hemlock forest. Ecosystems, 10, 1133–1147.CrossRefGoogle Scholar
  24. Garten, C. T., & Hanson, P. J. (1990). Foliar retention of N-15-nitrate and N-15-ammonium by red maple (Acer rubrum) and white oak (Quercus alba) leaves from simulated rain. Environmental and Experimental Botany, 30, 333–342.CrossRefGoogle Scholar
  25. Garten, C. T., Schwab, A. B., & Shirshac, T. L. (1998). Foliar retention of N-15 tracers: implications for net canopy exchange in low- and high-elevation forest ecosystems. Forest Ecology and Management, 103, 211–216.CrossRefGoogle Scholar
  26. Gilliam, F. S. (2006). Response of the herbaceous layer of forest ecosystems to excess nitrogen deposition. Journal of Ecology, 94, 1176–1191.CrossRefGoogle Scholar
  27. Gundersen, P., Schmidt, I. K., & Raulund-Rasmussen, K. (2006). Leaching of nitrate from temperate forests—effects of air pollution and forest management. Environmental Reviews, 14, 1–57.CrossRefGoogle Scholar
  28. Hagen-Thorn, A., Varnagiryte, I., Nihlgard, B., & Armolaitis, K. (2006). Autumn nutrient resorption and losses in four deciduous forest tree species. Forest Ecology and Management, 228, 33–39.CrossRefGoogle Scholar
  29. Haines, B. L., Jernstedt, J. A., & Neufeld, H. S. (1985). Direct foliar effects of simulated acid-rain.2. Leaf surface characteristics. The New Phytologist, 99, 407–416.CrossRefGoogle Scholar
  30. Hall, D. M., & Burke, W. (1974). Wettability of leaves of a selection of New Zealand plants. New Zealand Journal of Botany, 12, 283–298.Google Scholar
  31. Hall, D. M., Matus, A. I., Lamberto, J., & Barber, H. N. (1965). Infra-specific variation in wax on leaf surfaces. Australian Journal of Biological Science, 18, 323–332.Google Scholar
  32. Hansen, K., Draaijers, G. P. J., Ivens, W. P. M. F., Gundersen, P., & Vanleeuwen, N. F. M. (1994). Concentration variations in Rain and Canopy throughfall collected sequentially during individual rain events. Atmospheric Environment, 28, 3195–3205.CrossRefGoogle Scholar
  33. Harrison, A. F., Schulze, E.-D., Gebauer, G., & Bruckner, G. (2000). Canopy uptake and utilization of atmospheric pollutant nitrogen. In E.-D. Schulze (Ed.), Carbon and nitrogen cycling in European forest ecosystems (pp. 171–188). Berlin: Springer.Google Scholar
  34. Herwitz, S. R. (1985). Interception storage capacities of tropical rainforest canopy trees. Journal of Hydrology, 77, 237–252.CrossRefGoogle Scholar
  35. Hikosaka, K. (2005). Leaf canopy as a dynamic system: ecophysiology and optimality in leaf turnover. Annals of Botany, 95, 521–533.CrossRefGoogle Scholar
  36. Holloway, P. J. (1969). Effects of superficial wax on leaf wettability. The Annals of Applied Biology, 63, 145–153.CrossRefGoogle Scholar
  37. Houle, D., Ouimet, R., Paquin, R., & Laflamme, J. (1999). Interactions of atmospheric deposition with a mixed hardwood and a coniferous forest canopy at the Lake Clair Watershed (Duchesnay, Quebec). Canadian Journal of Forest Research-Revue Canadienne De Recherche Forestiere, 29, 1944–1957.CrossRefGoogle Scholar
  38. Laubhann, D., Sterba, H., Reinds, G. J., & De Vries, W. (2009). The impact of atmospheric deposition and climate on forest growth in European monitoring plots: an individual tree growth model. Forest Ecology and Management, 258, 1751–1761.CrossRefGoogle Scholar
  39. Levy, Y., & Horesh, I. (1984). Importance of penetration through stomata in the correction of chlorosis with iron salts and low-surface-tension surfactants. Journal of Plant Nutrition, 7, 279–281.CrossRefGoogle Scholar
  40. Lumme, I. (1994). Nitrogen uptake of Norway spruce (Picea-abies Karst) seedlings from simulated wet deposition. Forest Ecology and Management, 63, 87–96.CrossRefGoogle Scholar
  41. Lumme, I., & Smolander, A. (1996). Effect of nitrogen deposition level on nitrogen uptake and bud burst in Norway spruce (Picea abies Karst.) seedlings and nitrogen uptake by soil microflora. Forest Ecology and Management, 89, 197–204.CrossRefGoogle Scholar
  42. Magnani, F., Mencuccini, M., Borghetti, M., Berbigier, P., Berninger, F., Delzon, S., et al. (2007). The human footprint in the carbon cycle of temperate and boreal forests. Nature, 447, 848–850.CrossRefGoogle Scholar
  43. Maier-Maercker, U. (1983). The role of peristomatal transpiration in the mechanism of stomatal movement. Plant, Cell & Environment, 6, 369–380.CrossRefGoogle Scholar
  44. Millard, P., & Proe, M. F. (1993). Nitrogen uptake, partitioning and internal cycling in Picea sitchensis (Bong.) Carr. as influenced by nitrogen supply. The New Phytologist, 125, 113–119.CrossRefGoogle Scholar
  45. Millard, P., & Thompson, C. M. (1989). The effect of the autumn senescence of leaves on the internal cycling of nitrogen for the spring growth of apple trees. Journal of Experimental Botany, 40, 1285–1289.CrossRefGoogle Scholar
  46. Monks, P. S., Granier, C., Fuzzi, S., Stohl, A., Williams, M. L., Akimoto, H., et al. (2009). Atmospheric composition change—global and regional air quality. Atmospheric Environment, 43, 5268–5350.CrossRefGoogle Scholar
  47. Mussche, S., Samson, R., Nachtergale, L., De Schrijver, A., Lemeur, R., & Lust, N. (2001). A comparison of optical and direct methods for monitoring the seasonal dynamics of leaf area index in deciduous forests. Silva Fennica, 35, 373–384.Google Scholar
  48. Nadelhoffer, K. J., Emmett, B. A., Gundersen, P., Kjonaas, O. J., Koopmans, C. J., Schleppi, P., et al. (1999). Nitrogen deposition makes a minor contribution to carbon sequestration in temperate forests. Nature, 398, 145–148.CrossRefGoogle Scholar
  49. Neary, A. J., & Gizyn, W. I. (1994). Throughfall and stemflow chemistry under deciduous and coniferous forest canopies in south-central Ontario. Canadian Journal of Forest Research-Revue Canadienne De Recherche Forestiere, 24, 1089–1100.CrossRefGoogle Scholar
  50. Niinemets, U., & Tamm, U. (2005). Species differences in timing of leaf fall and foliage chemistry modify nutrient resorption efficiency in deciduous temperate forest stands. Tree Physiology, 25, 1001–1014.Google Scholar
  51. Peuke, A. D., Jeschke, W. D., Dietz, K. J., Schreiber, L., & Hartung, W. (1998). Foliar application of nitrate or ammonium as sole nitrogen supply in Ricinus communis—I. Carbon and nitrogen uptake and inflows. The New Phytologist, 138, 675–687.CrossRefGoogle Scholar
  52. Rennenberg, H., & Gessler, A. (1999). Consequences of N deposition to forest ecosystems—recent results and future research needs. Water, Air, and Soil Pollution, 116, 47–64.CrossRefGoogle Scholar
  53. Rennenberg, H., Kreutzer, K., Papen, H., & Weber, P. (1998). Consequences of high loads of nitrogen for spruce (Picea abies) and beech (Fagus sylvatica) forests. The New Phytologist, 139, 71–86.CrossRefGoogle Scholar
  54. Sampson, D. A., Janssens, I. A., & Ceulemans, R. (2006). Under-story contributions to stand level GPP using the process model SECRETS. Agricultural and Forest Meteorology, 139, 94–104.CrossRefGoogle Scholar
  55. Sase, H., Takahashi, A., Sato, M., Kobayashi, H., Nakata, M., & Totsuka, T. (2008). Seasonal variation in the atmospheric deposition of inorganic constituents and canopy interactions in a Japanese cedar forest. Environmental Pollution, 152, 1–10.CrossRefGoogle Scholar
  56. Schreiber, L., Skrabs, M., Hartmann, K. D., Diamantopoulos, P., Simanova, E., & Santrucek, J. (2001). Effect of humidity on cuticular water permeability of isolated cuticular membranes and leaf disks. Planta, 214, 274–282.CrossRefGoogle Scholar
  57. Sievering, H., Tomaszewski, T., & Torizzo, J. (2007). Canopy uptake of atmospheric N deposition at a conifer forest: part I—canopy N budget, photosynthetic efficiency and net ecosystem exchange. Tellus Series B-Chemical and Physical Meteorology, 59, 483–492.CrossRefGoogle Scholar
  58. Solberg, S., Dobbertin, M., Reinds, G. J., Lange, H., Andreassen, K., et al. (2009). Analyses of the impact of changes in atmospheric deposition and climate on forest growth in European monitoring plots: a stand growth approach. Forest Ecology and Management, 258, 1735–1750.CrossRefGoogle Scholar
  59. Sparks, J. P. (2009). Ecological ramifications of the direct foliar uptake of nitrogen. Oecologia, 159, 1–13.CrossRefGoogle Scholar
  60. Staelens, J., Houle, D., De Schrijver, A., Neirynck, J., & Verheyen, K. (2008). Calculating dry deposition and canopy exchange with the canopy budget model: review of assumptions and application to two deciduous forests. Water, Air, and Soil Pollution, 191, 149–169.CrossRefGoogle Scholar
  61. Sutton, M. A., Burkhardt, J. K., Guerin, D., Nemitz, E., & Fowler, D. (1998). Development of resistance models to describe measurements of bi-directional ammonia surface-atmosphere exchange. Atmospheric Environment, 32, 473–480.CrossRefGoogle Scholar
  62. Thimonier, A., Schmitt, M., Waldner, P., & Rihm, B. (2005). Atmospheric deposition on Swiss long-term forest ecosystem research (LWF) plots. Environmental Monitoring and Assessment, 104, 81–118.CrossRefGoogle Scholar
  63. Thomas, R. Q., Canham, C. D., Weathers, K. C., & Goodale, C. L. (2010). Increased tree carbon storage in response to nitrogen deposition in the US. Nature Geoscience, 3, 13–17.CrossRefGoogle Scholar
  64. Tyree, M. T., Scherbatskoy, T. D., & Tabor, C. A. (1990). Leaf cuticles behave as asymmetric membranes—evidence from the measurement of diffusion potentials. Plant Physiology, 92, 103–109.CrossRefGoogle Scholar
  65. Vallano, D. M., & Sparks, J. P. (2008). Quantifying foliar uptake of gaseous nitrogen dioxide using enriched foliar delta N-15 values. The New Phytologist, 177, 946–955.CrossRefGoogle Scholar
  66. Verstraeten, A., Sioen, G., Neirynck, J., Genouw, G., Coenen, S., Van der Aa, B., et al. (2007). Bosvitaliteitsinventaris, meetnet intensieve monitoring bosecosystemen en meetstation luchtverontreiniging: resultaten 2006, Rapporten van het Instituut voor Natuur-en Bosonderzoek 2007. Geraardsbergen, UK: Instituut voor Natuur-en Bosonderzoek.Google Scholar
  67. Vitousek, P. M., Aber, J. D., Howarth, R. W., Likens, G. E., Matson, P. A., Schindler, D. W., et al. (1997). Human alteration of the global nitrogen cycle: sources and consequences. Ecological Applications, 7, 737–750.Google Scholar
  68. VMM (2007). ‘Zure regen’ in Vlaanderen, Depositiemeetnet verzuring 2005–2006.Google Scholar
  69. Wilson, E. J., & Tiley, C. (1998). Foliar uptake of wet-deposited nitrogen by Norway spruce: an experiment using N-15. Atmospheric Environment, 32, 513–518.CrossRefGoogle Scholar
  70. Wuyts, K., De Schrijver, A., Staelens, J., Gielis, M., Geudens, G., & Verheyen, K. (2008). Patterns of throughfall deposition along a transect in forest edges of silver birch and Corsican pine. Canadian Journal of Forest Research-Revue Canadienne De Recherche Forestiere, 38, 449–461.CrossRefGoogle Scholar

Copyright information

© Springer Science+Business Media B.V. 2010

Authors and Affiliations

  • Sandy Adriaenssens
    • 1
  • Jeroen Staelens
    • 1
    • 2
  • Karen Wuyts
    • 1
    • 3
  • An de Schrijver
    • 1
  • Shari Van Wittenberghe
    • 3
  • Tatiana Wuytack
    • 3
  • Fatemeh Kardel
    • 3
  • Kris Verheyen
    • 1
  • Roeland Samson
    • 3
  • Pascal Boeckx
    • 2
  1. 1.Laboratory of ForestryGhent UniversityGontrode (Melle)Belgium
  2. 2.Laboratory of Applied Physical Chemistry—ISOFYSGhent UniversityGhentBelgium
  3. 3.Department of Bioscience EngineeringUniversity of AntwerpAntwerpenBelgium

Personalised recommendations