Air Pollution and Forest Decline Volume II

Air Pollution and Forest Decline

Volume II

Oxf .: 48 : 425.1 181.45 : 971

edited by J0rg B. Bucher and Inga Bucher-Wallin

Proceedings of the 14th International Meeting

for Specialists in Air Pollution Effects on Forest Ecosystems International Union of Forest Research Organizations

Project Group P2.05

held at lnterlaken, Switzerland, 2-8 October, 1988

Published by

Eldgenossische Anstalt for das forstliche Versuchswesen (EAFV)

CH-8903 Birmensdorf, Switzerland 1989

ISBN 3-905620-01-4

J.B. Bucher I. Bucher-Wallin

Eidgenossische Anstalt fur das forstliche Versuchswesen Swiss Federal Institute of Forestry Research (SFIFR) CH-8903 Birmensdorf, Switzerland

Manuscripts: provided by the authors

ABSTRACT

Bucher, Jurg B.; Bucher-Wallin, Inga (Editors) Air Pollution and Forest Decline

Proceedings of the 14th International Meeting for Specialists in Air Pollution Effects on Forest Ecosystems, International Union of Forestry Research Organizations, IUFRO Project Group P2.05, Interlaken, Switzerland, 2-8 October, 1988.

Birmensdorf: Eidgenossische Anstalt fur das forstliche Versuchswesen, 1989. Vol.I. 372 p., Vol.II. 192 p.

ISBN 3-905620-01-4.

Volume I contains 58 contributions grouped according to the sessions: Opening Session, I: Forest declines, II-A: Input of air pollutants, II-B: Biochemical and physiological effects, II-C:

Interaction with abiotic stress, III-A: Diagnosis and bioindica­

tors, III-B: Growth effects, III-C: Interaction with biotic stress, III-D: Genetical effects, III-E: Silvicultural measures and forest policy

Volume II contains 60 posters covering almost all the sessions of Volume I but with emphasis on biochemical and physiological effects and diagnosis.

Available from:

F. Fluck-Wirth, Internationale Buchhandlung fur Botanik und Naturwissenschaften, CH-9053 Teufen, Switzerland

Cover picture: Research site Lagern. View from the experimental tower over the open-top chambers and the measuring cabin.

Photo: R. Hasler, EAFV fill 4.89 A/47282

CONTENTS

Page Ahrend, R., Kahle, H., Breckle, s.-W.: Effect of cadmium on transpiration of young beech

trees (Fagus silvatica L.) 381

Ashmore, M.R., McHugh, F.M., Mepsted, R., Garetty, C.: Effects of ozone and acid mist on

saplings of Fagus sylvatica 384

Bendetta, G.: Schadstoffeintrag durch Niederschlage in Sudtirol 387 Citerne, A., Dizengremel, P., Pierre, M., Queiroz,

o.:

spruce clones submitted to controlled pollution and from healthy and diseased trees 390 Cox, R.M., Spavold-Tims, J., Hughes, R.N.: Coastal white birch deterioration in areas

receiving acid fog and other air pollutants around the Bay of Fundy, Canada 393 De Vuono, Y.s., Lopes M.I.M.S., Domingos, M.: Air pollution and effects on soil and vege-

tation of Serra do Mar, near Cubatao, Sao Paolo, Brazil 396

Derome, J.: Cation mobility in forest soils 399

Egger, A., Landolt, reduction in needles from spruce trees (Picea abies L.)

w.,

Immissionsekologische Untersuchungen am Wald im Kanton Zurich 404 Freer-Smith, P.H., Dobson, M., Taylor, G.: Factors controlling the rates of 03 uptake by spruce and beech 407 Gasch, G., Grunhage, L., Jager, H.-J., Wentzel, K.-F.: Das Schwefelfraktionsverhaltnis in

Fichtennadeln - Ein Indikator fur Immissionsbelastungen durch Schwefeldioxid 410 Gross, K., Wagner, E.: Measurements of gas exchange in young spruce saplings during fumi-

gation with ozone in combination with nitrogen dioxide and/or sulphur dioxide at the

time of shoot growth 413

Gunthardt-Goerg, M.S.: Site-dependant changes in the epicuticular wax structure of spruce 416 Guttenberger, H., Egger, G., Sevcik, G., Trenkler, I., Grill, D.: Water- and ionpermeabi-

lity after influence of triethyl lead 419

Hasler, Th., Schuepp, H., Ruegg, J.: Health status of large, solitary fruit trees in

Switzerland 422

Hasler, Th., Schuepp, H., Ruegg, J.: Injury factors associated with decline of large,

solitary fruit trees in Switzerland 425

Hocevar, M., Hladnik, D.: Norway spruce decline on alpine plateau in Slovenia 427 Holopainen, T., Nygren, P.: Responses in Scots pine needle ultrastructure to simulated

acid rain and potassium deficiency 430

Hepker, K.-A., Fuhrer, G., Strube, D., Senser, M.: Effects of extreme ozone concentra- tions on the physiology of Picea abies (L.) Karst. as related to the mineral nutrient

supply of the trees 433

Joos, K.A.: Investigation of a possible direct influence of highway traffic on nearby

woods 436

Joos, K.A., Stager, Chr.: Investigation of any possible influence of high frequency

electromagnetic fields on wood 439

Kahle, H., Breckle, s.-W.: Single and combined effects of lead and cadmium on young beech

trees (Fagus silvatica L.) 442

Karenlampi, L., Oksanen, J., Anttonen, T.: Growth rate of epiphytic lichens as a

bioindicator 445

Keller, T., Matyssek, R.: Dose effects of ozone on CO2 uptake and twig growth in spruce 447 Kempf, A.: Online information retrieval on air pollution and forest decline: Some search

examples from bibliographic databases 449

Kern, T., Grill, D., Bermadinger, E., Guttenberger, H.: Physiological reactions of

spruces in inversion zones 452

Khorasani, N.: Vorzeitiger Laubfall und Absterben der Platanen in Teheran 455 Kirkwood, I.A., Magan, N., McLeod, A.R.: Effect of atmospheric sulphur dioxide on the

phylloplane mycoflora of conifer needles 457

Kluczynski, B.: Utility of the early test in the estimation of tolerance of trees and

shrubs to the action of the fluorine compounds 460

Kontic, R., Muller-Jaag, R., Braker, o.u., Nizon, V.: Jahrringanalytische Untersuchungen

im Sihlwald (Kanton Zurich, Schweiz) 463

Langebartels, c., Fuhrer, G., Hackl, B., Heller,

w,

fumigation 466

Leonardi, s., Fluckiger, W.: Physiologische Auswirkungen der durch sauren Nebel induzier-

ten Kationenauswaschung aus Buchenblattern 470

Lesinski, J.A., Westman, L.: Visible symptoms of Norway spruce decline 474 Ling, K.A., Power, S.A., Ashmore, M.R.: A survey of the health of Fagus sylvatica in

Southern Britain 477

Mejnartovicz, L.E., Kopcewicz, J.: Endogenous growth substances in Scots pine trees of

different sensitivity to fluoride and SO2 480

Miller-Weeks, M., Spruce, J., Levesque, B., Smoronk, D., Cooke, R., Cox, s., Millers, I.:

Monitoring of red spruce and balsam fir decline in the Northeastern United States:

Symptomatology and mortality mapping -483

Murthy, M.S.R., Raza, S.H., Ahmed, A.: A new method in evaluation of sulfurdioxide

tolerance of certain trees 486

Nojd, P.: The correlation between estimated needle loss and diameter increment - preli-

minary results 489

Ojanpera, K., Huttunen, S.: Ozone fumigation accelerates surface erosion on Norway spruce

needles 490

Percy, K.E., Baker, E.A.: Effect of simulated acid rain on foliar uptake of Rb⁺ and so4²-

by two clones of Sitka spruce (Picea sitchensis (Bong.) Carr.) 493 Peterson, C.E.: Statistical issues for seedling studies in air pollution research 496 Pfirrmann, T., Albrecht, u., Kloos, M., Riebeling, R.: Effects of chloroform washing on

the elemental contents of needles of Picea abies (L.) Karst from the Taunus Mountains

(Hessen, FRG) 499

Pfirrmann, T., Eisenmann, T, Kloos, M., Payer, H.-D.: Effects of acid mist and ozone on the nutrition status of clonal Norway spruce after fourteen months of treatment in

environmental chambers 503

Pfirrmann, T., Kloos, M., Payer, H.-D., Blank, L.W.: Growth response of clonal Norway

spruce to 14-month-exposure to ozone and acid mist 507

Reinikainen, J., Huttunen, S.: Pine needle ultrastructure in an acid rain treatment 510 Salemaa, M., Jukola-Sulonen, E.-L.: Visually estimated defoliation class vs. other condi-

tion variables in Picea abies 513

Schoggl, W.: Zonierung der Schwefelbelastungsgebiete aufgrund der Schwefelgehalte in Fichtennadeln unter Berucksichtigung der orografischen und meteorologischen

Verhaltnisse 514

Schon, B., Wimmer, R., Wuggenig,

w.,

suchungen an Fichten aus osterreichischen Waldschadensgebieten 517 Schuepp, P., Comtois, P., Schemenauer, R.: Studies on pollution-induced nutrient stress

and reduction in pollen viability in high elevation forests 5²0 Senser, M., Payer, H.-D.: The frost hardiness of young conifers exposed to different

loads of ozone, sulfur dioxide or nitric oxide in environmental chambers 5²3 Sharma, G.K.: Cuticular and morphological dynamics in Salix nigra L. and Quercus alba L.

in relation to air pollution 5²7

Tichy, J.: A contribution to the method of ocular evaluation of forest stands as a whole 530 Tichy, J.: Twenty-five years' experiences with Picea pungens in heavy polluted areas 53²

376

Turunen, M., Huttunen,

s.:

Norway spruce seedlings after acid precipitation 535

Van der Eerden, L.J., Lekkerkerk, L.J.A., Smeulders, S.M., Jansen, A.E.: Effects of ozone

and ammonia on Douglas fir (Pseudotsuga menziesii) 538

Van der Eerden, L.J., Van den Ancker, H.A.M., Loedeman, J.H.: Assessment of tree vitality

on colour (CIR) and multi-spectral photography (MSP) 541

Vuorinen, M.: Effects of acid rain on an Ascocalyx abietina infection in Scots pine 544 Werner, H.: Die Ozonkerze - ein passiver Integrator zur flachendeckenden Abschatzung der

Ozonimmission 547

Wieser, G., Havranek, W.M., Bodner, M.: Ozone fumigation of Norway spruce at timberline 550 Zellnig, G., Bermadinger, E., Gailhofer, M., Grill, D.: Structural investigations (TEM,

SEM) of spruce needles from inversion-zones 553

Index of authors and coauthors, Vol. I 557

Index of authors and coauthors, Vol. II 558

List of participants 559

Poster Session

Chairman:

Werner Landolt

Air Pollution and Forest Decline (J.B. Bucher and I. Bucher-Wallin, eds.).

Proc. 14th Int. Meeting for Specialists in Air Pollution Effects on Forest Ecosystems IUFRO P2.0S, Interlaken, Switzerland, Oct. 2-8, 1988. Birmensdorf, 1989, p. 381-383. '

EFFECT OF CADMIUM ON TRANSPIRATION OF YOUNG BEECH TREES (FAGUS SILVATICA L.)

R. Ahrend, H. Kahle & S.-W. Breckle

Bielefeld University, Faculty of Biology, Dept. of Ecology POB 8640, D-4800 Bielefeld (F.R.G.)

ABSTRACT

Young beech trees (Fagus silvatica L.) were planted into a Cd-contaminated forest soil with increasing concentrations from O ppm to 6.0 ppm. Transpiration, stomata! resistance and climatic datas were measured with a Steady State Porometer. Nearly all treatments with Cd showed a decrease of transpiration rates com­

pared with controls. The main cause for lower­

ing the transpiration seems to be the high accumulation of Cd in roots or xylem obstruc­

tions and not a defect of stomata! function, because of the increasing diffusive resistance related to the decrease of transpiration. Also the significant correlation between relative humidity and transpiration of each treatment indicates that stomata! mechanism is not affected.

INTRODUCTION

Cadmium as well as other heavy metals are long-range transported air pollutants, which have been deposited and accumulated for de­

cades in forest ecosystems ( ELLENBERG et al.

1986). Several authors observed decreased transpiration rates and increased stomata!

resistance in Cd-treated plants (BAZZAZ et al.

1974, KIRKHAM 1978). Investigations have shown that in Fagus silvatica L. adverse effects of Pb and Cd start with concentration levels, which are not far from those occuring in forest stands (KAHLE 1988). All these experi­

ments , however, were carried out with plants growing in hydroponics or in sand culture with optimal supply of nutrient solution, but not in soil,being the natural substrat for plants.

The question in our investigation is, whether

Fagus silvatica L,,

MATERIALS AND METHODS

In April 1987 young beech trees (8-13 years old) were taken from a rejuvenated forest stand and transplanted into pots with a sandy forest soil (upper mineral layer, pH(H20)=3.8) contaminated with Cd(N03)2. The Cd-conceritra­

tions (plant available fractions, defined as ammoniumacetate-extractions) were : O / 0.5 / 1.0 / 1.5 / 2.0 / 2.5 / 3.0 / 3.5 / 4.0 / 4.5 / 5.0 / 5.5 / 6.0 ppm Cd. Plants were kept to adapt to open air conditions for 3 months before experimentation started. Transpiration and stomata! resistance was measured by a Licor Steady State Porometer (Li 1600) several times in the morning in July, August and early in September. Climatic datas were recorded with the Porometer and with the thermohygro­

graph.

RESULTS AND DISCUSSION

Transpiration of young beech trees, even under low heavy metal stress, is clearly shown to be lowered. Results presented in Figure 1 show that transpiration rates decreased with in­

creasing concentration of Cd in the soil.

Treatments with 5.5 ppm and 6.0 ppm Cd signi­

ficantly lowered the rate of transpiration by about 20%, compared with controls. At the same time an increased stomata! resistance could be observed (Fig.2). Experiments with hydroponi­

cally grown 2-years old beech seedlings in nutrient solution after only 7 days with 5 ppm Cd show similar results (HAGEMEYER et al.

1986). BAZZAZ et al.(1974) suggested that the initial response of corn and sunflower leaves with various burdens of Cd may be stomata!

closure. Partial regression analysis shows correlation between transpiration and light quantum, transpiration and leaf temperature, as a function of the air temperatur ( GATES 1968), and between relative humidity and transpiration (Tab.1), but multiple regression analysis gives us the hint, that only relative humidity has the greatest correlation coeffi­

cient of these three climatic parameters.

However, generally the percentages explaining the dependence of transpiration on relative humidity is very low (max 27. 4 % ) , so that there remains a great part of variance unex­

plained. This means that other parameters have to be investigated in order to explain low transpiration rates and high stomata! re­

sistance. LAMOREAUX and CHANEY (1977) suppose that xylem obstructions by Cd-induced cell wall degraded products might be a cause of reduced water transport. This is shown by EM­

studies by Barcelo et al.(1988). The reduction mainly may take place in the roots of beech seedlings, because they accumulate Cd in roots to a rather high level when grown in this soil as RODER (1987) has shown. At present there is no reliable extrapolation of these results to adult grown trees in forests possible, but they indicate at least that the minimal con­

centrations of Cd for exertion of toxic effects are in the range of the present-day concentrations in acidified forest soils in Central Europe.

ACKNOWLEDGEMENTS

This investigation was partly supported by the

"Ministerium fur Umwelt, Raumordnung und Land­

wirtschaft" of Nordrhein-Westfalen (F.R.G.).

REFERENCES

Barcelo, M., Vazquez, M.D.

Poschenrieder, Ch. 1988: Cadmium-induced structural and ultrastructural changes in the vas­

cular system of bush bean stems, Bota­

nica Acta 3, 254-261.

Bazzaz, F.A., Rolfe, G.L.

Carlson, R.W.

197 4: Effect of Cd on photosynthesis and transpiration of excised leaves of corn and sunflower, Physiol. Plant. 32:

373-376.

Ellenberg, H. , Mayer, R.

Schauermann, J.

(eds.) 1986: 6kosystemforschung. Ulmer Verlag Stuttgart.

Gates, D.M. 1968: Transpiration and leaf tem­

perature, Annual Rewiev of Plant Phy­

siology 19, 211-238.

Hagemeyer, J. , Kahle, H.

Breckle, S. -W.

1986: Cadmium in Fagus sylvatica L., trees and seedlings: leaching, uptake and interconnection with transpiration, Water, Air and Soil Pollution 29, 347-359.

Kahle, H. 1988: Wirkung von Blei und Cadmium auf Wachstum und Mineralstoffhaushalt von Jungbuchen (Fagus

L.) in Sandkul tur, Doct. Thesis Bielefeld Uni­

versity, 220p.

Kirkham, M.B. 1978: Water relations of cad­

mium-treated plants, J. Environ. Qual., Vol.7 no.3.

382

Lamoreaux, R. J. ^& Chaney, W.R. 1 9 77 : Growth and water movement in silver maple seedlings affected by cadmium, J. En­

viron. Qual., 201-205.

Roder, u. 1987: Der EinfluB von Pb und Cd auf das Wachstum und den Kationenhaushalt von Buchenkeimlingen (Fagus ^sylvatica L.) , Dipl. Thesis Bielefeld Universi­

ty, 144p.

Tab. 1: Partial correlation between transpira­

tion rates and light quantum, relative humidity and leaf temperature (* signi­

ficance 5 %, ** significance 1 %), depending on increasing soil concentra­

tions of Cd.

PARTIAL CORRELATION COEFFICIENTS Cd-Conc.

(ppm) Light Humidity Leaf Temp.

0 .111 -.418* .208 0.5 .182 -.481** .298 1.0 .157 -.469** .323 1.5 .189 -.454** .184 2.0 .309 -.454** .211 2.5 .272 -.422* .208 3.0 .260 -.487** .304 3.5 .366* -.533** .338 4.0 .288 -.473** .314 4.5 .265 -.435* .275 5.0 .302 -.536** .282 5.5 . 311 -.512** .302 6.0 .276 -.500** .314

1

-

C\I

'E

Cl �

C: 0 :;::::

·a

8.5 8.0 7.5 7.0 6.5 6.0 September

4.5 5.0

1.0 1.5 2.0 2.5 3.0 ^3.5 4.0

0 ^0.5

concentration ( ppm Cd )

Fig.1: The effect of Cd concentration on transpiration rates measured with a Steady State Porometer. Means of July, August and September 1987,

-

....

N•

'en 'E

C) �

-

:;:::: 0

·a.

8.5�---..3.0 8.0

7.5 7.0 6.5

6.0

o{

., _{., ..} , ·-· -·-·-·-· -·-

.. ,.,

- ^{. . ... ,·'} ···•·•··

·-·-···-•-•.,..., ...

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·-·-···- .. .

•··· ···•·•

___ .---.�����=�---,

1.0

I I I I I I I I I I

Jo

1.0 1.5 2.0 2.5 3.0 3.5 4.0 4.5 5.0 5.5 6.0

Concentration ( ppm Cd )

Fig.2: Transpiration rates (see Fig.1) compared with diffusive resistances of the upper leaves of young beech trees depending on increasing soil concentrations of Cd.

Cl) 0 C: a,

-

'in

&

'in � ::,

--

5.5

LEGEND Left Scale

Transp. July Transp. August Transp. September Right Scale

Diff. Res. July

·-·-·-·-·-·

Air Pollution and Forest Decline (J.B. Bucher and I. Bucher-Wallin, eds.).

Proc. 1 4th Int. Meeting for Specialists in Air Pollution Effects on Forest Ecosystems, IUFRO P2.05, Interlaken, Switzerland, Oct. 2-8, 1 988. Birmensdorf, 1 989, p. 384-386.

EFFECTS OF OZONE AND ACID MIST ON SAPLINGS OF FAGUS SYLVATICA M.R. Ashmore, F.M. McHugh, R. Mepsted and C. Garretty

Department of Pure and Applied Biology, Imperial College of Science and Technology, Silwood Park, Ascot, Berks SL5 7PY, U.K.

ABSTRACT

Fagus sylvatica saplings were exposed for 8 months to three o3 exposure regimes 1n com­

bination with mist at pH 4.8 or pH 3.5. Leaf fall was accelerated at high o3 concentrations and low mist pH and there was evidence of a synergistic interaction. Leaf dry weight after budburst in the subsequent season was reduced at high ozone (03) concentrations, primarily due to a reduced leaf size, but stem dry weight was increased. Fagus sylvatica saplings were also exposed outdoors for 9 months to mist at six acidities ranging from pH 5.4 to pH 2.5. Shoot extension during the experiment was greatest at intermediate pH's;

however, both leaf and root dry weight after budburst in the subsequent season were reduced at intermediate pHs. Calcium content of these new leaves decreased linearly with decreasing mist pH. The results demonstrate that o3 and mist acidity may affect tree performance both immediately, and in seasons subsequent to exposure.

INTRODUCTION

The widespread decline in forest health in Western Europe over the past decade has affected a number of tree species, including Fagus sylvatica. One of the major hypotheses proposed to explain this phenomena suggests that ozone and acid mists are the primary pollutants involved (Prinz et al., 1987). At high elevations, where damage is often severe, high o3 concentrations persist throughout day and night, unlike at lower elevations (Ashmore et al., 1985; Prinz et al., 1987); the fre­

quency of mists is alsogreater at higher elevations. We have investigated the effects of o1 concentrations typical of high and low elevation sites, in combination with acid mist, and the effects of a range of mist acidities, on saplings of Pinus sylvestris, Picea abies, Abies alba and Fagus sylvatica;

here we describe results obtained for Fagus sylvatica.

METHODS

The first experiment was carried out using two-year old potted saplings in six out­

door semi-open top chambers, receiving one of three o1 treatments (Ashmore et al., 1987).

The 'control' treatment provided a mean con­

centration of 27 ppb with no values above 50 ppb; the 'low elevation' treatment provided a fluctuating day/night cycle with a mean con­

centration of 29 ppb and 3.7% of hours with concentrations above 75 ppb; and the 'high elevation' treatment provided no day/night

384

cycle, with a mean concentration of 48 ppb and 10% of hours with concentrations above 75 ppb. These O treatments started in early May and finisXed in September 1986. From May to December 1986, plants were exposed over­

night for 10 h to mist at either pH 4.8 or pH 3.5 at approximately weekly intervals;

further details of the mist treatments are given by Ashmore et al. (1987). In January 1987, saplings were removed from the

chambers, and then kept outdoors until they were destructively harvested in June 1987.

The second experiment was carried out in open misting platforms. From June 1986 to February 1987, plants were exposed overnight for 10 h to mist, with droplet size 5-30 um, at one of six pHs (5.5, 4.8, 3.9, 3.5, 3.0 or 2.5) at approximately weekly intervals. Mist pH was varied by adding sulphate and nitrate to a stock so1¥iion ��ntaJning fixed+concen­

tr�tions of Ca , Mg , K , NH4 , Na and Cl • Plants were harvested in June 1987.

RESULTS

The course of leaf loss in the O /acid mist experiment was followed from lati Sept­

ember 1986. The results (Fig. 1) show that leaf loss proceeded more rapidly in plants receiving higher concentrations of O . Although mist acidity did not influe�ce the rate of leaf loss in 'control' and 'low elevation' o3 treatments, leaves were lost more rapidly from plants treated with pH 3.5 mist in the 'high elevation' treatment; a significant synergistic interaction between o3 treatment and mist acidity was found in late October (Ashmore et al., 1987). Leaf fall ceased by mid-December. Although total leaf ,numbers produced was not significantly affected by o1 treatment, a greater pro­

portion of leaves were lost from plants receiving higher o1 concentrations (Fig. 1);

in contrast, mist acidity had no significant effects on the proportion of leaves lost.

Neither O nor mist treatment signi­

ficantly affected the spring phase of shoot extension. However, a secondary flush of shoot growth occurred on many of the experi­

mental plants in August and September 1986.

The mean shoot length of this secondary growth was not affected by mist acidity, but was significantly greater in the 'low

elevation' and 'high elevation' o3 treat­

ments.

Results from the final harvest in June 1987, six months after the end of the experi­

mental treatments, showed no significant effect of either o3 or mist acidity on total

100 90 80 70 60

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30 20 10

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November December

Month

=-:: :: ^;:;>

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Figure 1. Cumulative leaf loss in autumn 1986.

50 45 40

i

-� ]

� ²⁰

15 10

0

'Control'

ozone 'Low elevation' 'Hie:h elevation' ozone 'Ozone CJ current season leaf and stem

B previous years' stem

• root

Figure 2. Distribution of dry matter in June 1987 in the three o3 regimes.

plant dry weight. However, significant effects of 0 on the distribution of dry matter were iound (Fig. 2). A greater per­

centage of dry matter was in the form of pre­

vious years' stem, and a smaller percentage in the form of the new season's leaf and stern growth, at higher 0 concentrations. The effect on older ste� material may partly be due to the greater secondary flush of growth produced in the previous year at higher con­

centrations. The reduction in dry weight of new season's growth was due primarily to a reduction in mean leaf size rather than in shoot length or leaf numbers.

The results from the second experiment, in which the dose-response relationship to mist acidity was examined outdoors, showed a complex pattern. There was a significant quadratic relationship between mist acidity and the number of leaves produced in the first season (Fig. 3a), with shoot length in­

creasing as pH dropped from 5.6 to 3.5, but then decreasing again between pH 3.5 and pH 2.5. However, data.from the final harvest in June 1987, four months after the end of the experimental period, showed very different results. Quadratic relationships were found for leaf dry weight and root dry weight (Fig.

3b), but in this case the values were lowest over the range pH 4.8 to pH 3.5, and greater at both higher and lower values of mist pH.

The effect on leaf dry weight may have been partly due to a reduced proportion of buds bursting at intermediate pHs. Mist acidity had no significant effect on the magnesium and potassium concentrations of these new leaves; however, calcium concentration de­

creased linearly with decreasing mist pH (Fig. 3c).

The concentrations of 0 used in this experiment were chosen as being typical of high elevation sites in central Europe, and of low elevation sites in central and

northern Europe. It is thus of considerable interest that significant effects on the growth of Fagus sylvatica saplings have been observed over the relatively short timescales of these experiments and at realistic o1 con­

centrations (Ashmore et al., 1985). The accelerated leaf lossinO in our experi­

ments is consistent with r�sults for Fagus sylvatica by Prinz et al. (1987). However, our results provide little support for the hypothesis that 0 and acid mist act syner­

gistically to cau�e decline in health of this species; the only significant interaction found was on the initial rate of leaf loss.

One reason for the lack of effects of mist in the chamber experiment may have been the levels of acidity used. Results from the outdoor mist dose-response study revealed no significant differences in terms of plant growth between pH 4.8 and pH 3.5, although treatment effects were found at both higher and lower pHs. The quadratic form of short term response of shoot growth may be inter­

preted as a positive response to increased sulphur and/or nitrogen supply at inter­

mediate pHs, followed by an adverse effect of acidity as pH drops further. However, this stimulation of shoot growth at moderate pHs was followed by a reduced leaf and root weight in the following year without further treatment.

240 220 200 180 160 140

� ¹²⁰

3

I

F ratio for Mist: 1.5 Linear: 1.0 Quadratic: 4.S•

6 s 4

Mist pH

3 2

(a) Leaf numbers produced (1986).

24 22 20 18

3

ii: 12 ₁₀

t

6 4 2 0 6

ILSD

T +,

:LSD ',,, -+----+----+

.,,..

'�---

Mist pH 4

F ratio for Mist:

Linear:

Quadratic:

root

�+ leaf

Leaf Root 1.0 2.7•

0.0 2.4 3.9 6.7•

(b) Leaf and root dry weight (1987).

F ratio for Mist: 2.1 Linear: 8.2•

Quadratic: 0.0 2

0 -1---�--..----,---.^-L--�----..---r---1

6 4

Mist pH

(cl New leaf calcium content (1987).

2

Figure 3. Effect of mist pH on (al Numbers of leaves produced during treatment period; (b) Dry weight of root, and

(cl Calcium content of leaves pro­

duced in the subsequent spring.

386

Indeed, in both experiments, a stimu­

lation of shoot growth in the year of treat­

ment, caused either by o3 or mist acidity, resulted (either directly or indirectly) in reduced new shoot growth in the subsequent season. This might have resulted from reduced input of assimilate to storage pools or adverse effects on bud viability. Keller (1979) has demonstrated that exposure to

so

in one season can adversely affect root growth of Picea abies in the subsequent year, but similar effects are not well established for o and mist acidity. Their existence demon�trates that immediate responses to pollutant exposure may be less important in terms of tree growth than longer-term effects carried over into subsequent years.

ACKNOWLEDGEMENTS

We thank Deborah Parsons and Tony Fletcher for their excellent technical assistance. This work was supported financially by the U.K. Department of the Environment.

REFERENCES

Ashmore, M.R., Bell, J.N.B. and Rutter, A.J.

(1985). The role of ozone in forest damage in West Germany. Ambio 14: 81- Ashmore, M.R., Garretty, C., McHugh, F.M. and 87.

Mepsted, R. (1987). Combined effects of ozone and acid mist on tree seedlings.

In: Air Pollution and Ecosystems. (P.

Mathy, ed.), pp. 659-664. D. Reidel, Dortrecht.

Keller, T. (1979). Der Einfluss langauernder SO - Begasungen auf des Wurzelwachstun def Fichte. Schweizeische Zeitschrift fur Forstwesen 130: 429-435.

Prinz, B., Krause, G.H.M. and Jung, K.-D.

(1987). Development and causes of novel forest decline in Germany. In: Effects of Atmospheric Pollutants on Forests, Wetlands and Agricultural Ecosystems.

(T.C. Hutchinson & K.M. Meema, eds.), pp. 1-24. Springer-Verlag, Berlin.

Air Pollution and Forest Decline (J.B. Bucher and I. Bucher-Wallin, eds.).

Proc. 14th Int. Meeting for Specialists in Air Pollution Effects on Forest Ecosystems, IUFRO P2.05, Interlaken, Switzerland, Oct. 2-8, 1988. Birmensdorf, 1989, p. 387-389.

SCHADST0FFEINTRAG DURCH NIEDERSCHLAGE IN SUDTIR0L Gunther Bendetta

Biologisches Labor der Autonomen Provinz Bozen-SUdtirol

EINLEITUNG

Durch den Einsatz fossiler Brennstoffe mit Beginn des industriellen Zeitalters wurden enorme Mengen an Kohlenstoff, Stickstoff, Schwefel, Phosphor und Schwermetallen in nur wenigen Jahrzehnten wieder freigesetzt. Dies fUhrte zu einer Veranderung der natUrlichen Zusammensetzung der Atmosphare und in der Folge zu einer Storung der geobiochemischen und biochemischen Kreislaufe. Die Verschiebung des natUrlichen Gleichgewichts zwischen sauren und alkalischen Substanzen fUhrte weltweit zu einem Absinken des pH-Wertes im Niederschlag, was zu einer zunehmenden Versauerung der aquatischen und terrestrischen 0kosysteme fUhrte. (Egner et al., 1955)

In SUdtirol begann man im Jahre 1983 im Rahmen des Untersuchungsprogramms "Waldzustands­

erfassung" das AusmaB und den Grad der Versauerung der Niederschlage und der Hoch­

gebirgsseen in kristallinen Einzugsgebieten zu untersuchen.

METH0DIK

An mehreren in Wald- und Stadtrandgebieten ge­

legenen MeBstellen in SUdtirol wurden "bulk"­

und "wet"-Depositionen erfaBt. Die geographische Lage der Standorte ist in Abb. 1 dargestellt.

Abbildung 1. Die Lage der MeBstationen des DepositionsmeBnetzes.

1-Eyrs (1153 m Seehohe), 2-Mahlbach (1219 m Seehohe), 3-Ritten (1780 m Seehohe),

4-Terenten (1140 m Seehohe), 5-Leifers (260 m Seehohe), 6-Montiggl (530 m Seehohe), 7-Fennberg (1160 m Seehohe)

Der Standort Montiggl stell te im Jahre 1984 eine der HauptmeBstationen im oberitalie­

nischen MeBstellennetz zur Untersuchung der sauren Niederschlage dar (Gruppo di Studio, 1987).

FUr die Erfassung der Depositionen wurden

"bulk-Sammler", bestehend aus einem Trichter (0 = 30 cm) und einer Polyathylenflasche (5 1) und "wet only-Sammelgerate" (an der MeBste.lle Montiggl und Ritten) eingesetzt.

In den Wochenproben wurde der pH-Wert (Glaselektrode) und die elektr. Lei tfahigkei t (Konduktometer) bestimmt, zudem noch die Komponenten S04, N03, Cl und NH4 (mittels Ionenchromatographie).

ERGEBNISSE

Die gewichteten Jahresmittel der MeBgroBen einzelnen MeBstellen sind in Tabelle angefUhrt. Der niedrigste mittlere pH-Wert 4, 72 trat an der Station Montiggl ( 1984)

der 1 von auf und die hochsten an der MeBstelle in Leifers (5,19 im Jahre 1985) und in Eyrs (5,15 im Jahre 1986). In Einzelproben jedoch traten Extremwerte im stark sauren Bereich auf: der niedrigste bisher gemessene pH-Wert betrug 3, 75 (Ri tten, im Dezember 1985). Die hochste Leitfahigkeit mit Werten zwischen 18,1 und 29,2 (Jahresmittel) wurden an der Station Lei­

fers ermittelt, ebenso die hochsten S04/S-Konzentrationen mit 0,90 bis 1,19 mg/1.

Die Konzentrationen fUr N03-N lagen an allen Stationen zwischen 0, 25 und 0, 55 mg/1. Die NH4-N Konzentrationen waren ungefahr in der gleichen GroBenordnung ( 0,29-0,68 mg/1). Die Cl-Konzentrationen bewegten sich zwischen 0,2 und o, 6 mg/1.

Zur Beurteilung der atmospharischen Schad­

stoffbelastung der jeweiligen Standorte muB neben der Konzentrationssi tuation die pro Zei t- und Flacheneinhei t deponierte Menge herangezogen werden. Die Flachenbelastung in g pro m² und Jahr ist in Tabelle 2 fUr die Jahre 1983 bis 1987 dargestellt. Was den Eintrag an Nitrat-Stickstoff, Ammonium-Stickstoff und Sulfat-Schwefel betrifft, ist die Station Fennberg die am hochsten belastete MeBstelle, gefolgt von Leifers, Ritten und Montiggl. Die MeBstelle Leifers wies zwar fUr alle Elemente

im Mittel hohere Konzentrationen auf als Tab. 2: Schadstoffeintrag durch Bulk- und Wet Fennberg , aber es wurden wegen der deutlich only-Deposition

hoheren Niederschlagsmenge hohere Eintrage (Angaben in g/m² *a) ermittelt.

Tab. 1 : Gewichtete Jahresmi ttel der Ionen- Mellstelle Niederschlag H+ Nll4-N 003-N 504-S Cl

konzentrationen im Niederschlag ^{( nm )}

(Angaben in mg/1) Bulk

Malbach 1983 871 , 9 0,010 0,35 0, 31 0,61 0 , 39 LF(US/20) So4-S 003-N Nll4-N Cl 1984 1001 , 4 0, 014 0, 29 0, 25 0, 58 0, 27 MeBstelle H+ pH-Wert

l\tJntiggl 1983 707 , 2 0,010 0,30 0,31 0,63 0 , 38 Bulk

0,011 4, 97 19, 6 0 , 69 0 , 35 0,41 0 , 5 1984 737, 8 0, 014 0, 25 0, 28 0, 61 0, 28 Malbach 1983

0,014 4 , 84 14, 4 0 , 58 0, 25 0 , 29 0 , 3 1985 680.2 0,008 0,39 0, 31 0,58 0 , 22

1984 1986 732,4 0,010 0,35 0,37 0,55 0, 19

Montiggl 1983 0, 014 4,85 21 , 0 0 , 89 0,44 0,43 0,5 1987 889 , 5 0,013 0, 40 0, 37 0, 65 0, 32 1984 0,019 4,72 19, 6 0 , 83 0,38 0,33 0 , 4 _Fennberg 1983 926 , 3 0,010 0, 50

1985 0, 012 4, 92 18, 5 0 , 85 0,46 0,58 0 , 3 0,42 0 , 77 0 , 55

0,75 0, 51 0,48 0 , 3 1984 1083,0 0, 016 0,40 0,35 0, 78 0 , 35

1986 0,014 4,84 18, 6

0 , 73 0,42 0,45 0, 4 1985 1107 , 6 0,013 0,59 0,43 0,85 0, 33

1987 0,014 4,85 17, 2 1986 980, 1 0, 018 0 , 53 0 , 54 0,81 0 , 33

Fennberg 1983 0, 011 4,95 21 , 3 0 , 83 0,46 0,53 0 , 6 1987 1262 , 4 0,020 0,57 0,49 1,02 0 , 52 1984 0,015 4 , 84 16, 9 0,72 0,32 0,37 0 , 3 _Leifers 1983 769 , 4 0,008 0,38 0 , 37 0,92

1985 0,012 4, 92 16, 2 0, 77 0,39 0, 53 0, 3 0,45

0, 3 1984 754, 2 0,006 0, 29 0,31 0,88 0,48

1986 0,018 4,75 21, 1 0,83 0, 55 0, 54 1985 762 , 2 0,005 0,52 0,38 0,87 0 , 34

1987 0,016 4,80 18, 1 0,80 0 , 39 0,46 0 , 4 1986 862 , 7 0,008 0,44 0,43 0, 78 0 , 33

Leifers 1983 0, 010 5,05 29 , 2 1 , 19 0 , 48 0,49 0 , 6 1987 896 , 6 0,007 0,43 0,38 0,86 0,48 1984 0,008 5, 10 22 , 3 1 , 16 0, 41 0,39 0, 6

Eyrs 1986 633, 8 0,004 0, 25

1985 0,006 5 , 19 22, 7 1 , 14 0,49 0,68 0,4 0, 21 0,38 0, 13

1986 0,009 5,07 20, 4 0,90 0 , 50 0, 51 0, 4 1987 562 , 9 0, 004 0,36 0, 22 0, 32 0, 17 1987 0,007 5 , 13 18, 1 0 , 95 0,42 0,48 0 , 5

Terenten 1986 753 , 4 0,009 0, 39 0, 31 0, 50 0,17 1987 930, 9 0,011 0,44 0,31 0,48 0, 22 (Jun1-Dez) 1985 1986 0,007 ( 5 , 55) 5 , 15 (12, 6) 15,0 (0,66) 0,60 (0, 34) 0 , 33 (0,67) (0,2) 0,39 0 , 2 _Ritten 1985 968, 5 0,011 0, 56 0,37 0, 75 0, 28

1987 0,008 5,11 16, 5 0 , 57 0,40 0, 64 0 , 3 1986 978,4 0, 016 0,43 0,39 0,59 0, 23

1987 1172 , 6 0,017 0,49 0,38 0,70 0 , 35 Terenten

(Juni-Dez) 1985 (4,99) (15,5) (0,78) (0, 38) (0, 58) (0 , 2) _Wet-only

1986 1987 0,012 0, 012 4,89 4 ,93 17, 8 13, 1 0,66 0 , 51 0 , 33 0,47 0 , 2 0, 42 0, 52 0, 2 l\tJntiggl 1985 680, 2 0, 010 0,38 0,27 0,50 0, 16 1986 732 , 4 0,012 0, 29 0, 28 0,36 0, 14 Ritten 1985 0,011 4 , 97 16, 3 0 , 76 0,38 0,58 0 , 3

1986 0,016 4,80 15,9 0,60 0, 40 0,44 0 , 2

1987 0,014 4,85 14, 4 0 , 60 0, 32 0,41 0 , 3 _{1 4 8 U L K}

1 2 Wet-only

Montiggl 1985 0, 015 4,85 16, 8 0 , 74 0 , 39 0,56 0, 2 _{1 0} 1986 0,016 4,80 15,0 0,49 0,39 0,39 0 , 2

D a

m m I U l K

• o

W E T 3 0

0 2· 1 0 1 2

..

Abb. 4: Vergleich

2 0 bulk-wet (S04 in mg/1)

Die Abbildungen 2 , 3 und 4 geben den Vergleich

1 0

der mit bulk- und mit wet-only Sammelgeraten

-

W E T ermittelten Ergebnisse wieder.

0

1 0 2 0 3 0 • o Die Ergebnisse in Abbildung 2 zeigen , daB die

Sammeleffektivitat des ¹¹wet-only¹¹-Gerates der des "bulk"-Gerates entspricht und daB somit Abb . 2 : Vergleich bulk-wet (Niederschlag) eine gute Funktionsweise des Regensensors

gegeben ist. Die pH-Werte der

I U L K "bulk"-Niederschlagsproben sind vielfach hoher

als die der "wet-only"-Proben, was auf die neutralisierende Wirkung der deponierten

'I, Staubpartikel im offenen Behalter zurlickzu-

.. .

konnten auch an der Station in Piacenza er- zielt werden, nicht jedoch in Pallanza, ^WO keine Unterschiede zwischen den zwe i

W E T Sammelsystemen gefunden wurden (Gruppo di

Studio , ^{1 987 ) .} Die Sulfat-Konzentrationen (Abbildung 4) sind in "bulk"-Proben hoher als Abb. 3 : Vergleich bulk-wet (pH-Wert) in ¹¹wet-only¹¹-Proben, was darauf hinweist , daB

388

an dieser Station Sulfat auch durch trockene Deposition eingetragen wird und daB ein gewisser Anteil davon mi t diesem Sammelgerat erfaBt wird . Ebenso fanden Soderland (1982) hohere Konzentrationen in "bulk"-Systemen als in "wet-only"-Sammlern .

DISKUSSION

Die mittleren pH-Werte liegen mit Ausnahme jener der MeBstellen in Leifers und in Eyrs nach der von Smidt (1983) zugrunde gelegten Bewertung im leicht sauren Bereich .

Die MeBstellen von Mahlbach, Eyrs, Terenten und Ri tten konnen als niedrig belastete MeBorte eingestuft werden ; sie weisen mittlere Leitfahigkeiten bis 20 uS/cm auf und Sulfat/S-Gehalte bis 0 , 80 mg/1 . Zu den deutlich beeinfluBten MeBstellen zahlen die Stationen Leifers und Fennberg, und tw . auch Montiggl .

Vergleicht man die Ergebnisse der Nie­

derschlagsanalysen einiger MeBstellen aus den Jahren 1983 bis 1987, so zeigt sich besonders an den MeBstationen in Leifers und in Montiggl eine leichte Abnahme der Sulfat/S-Konzentra­

tionen bzw . -Depositionen im Niederschlag (Tab . 1 u . 2) . Diese Abnahme ist auf den RUckgang der S02-Emissionen in diesem Gebiet zurUckzufUhren (Bendetta, 1988) . Ein ahnlicher Trend konnte auch an den Stationen in Reutte und Kufstein festgestellt werden (Landesforstdirektion, 1988), ebenso in Pallanza am Lago Maggiore (Moselle et al . , 1985) und in Hubbard Brock Ecosystem- USA

( Likens et al . , 1988) .

Der Vergleich der sUdtiroler Depositionsdaten mit den nordtiroler Werten zeigt, daB die durch "bulk"- bzw . "wet-only"-Deposi tionen eingetragenen Schadstoffelemente im Bereich jener Eintrage liegen, welche auch an den meisten MeBstellen Nordtirols ermittelt werden.

ZUSAMMENFASSUNG

Seit 1983 werden im Rahmen des Untersu­

chungsprogrammes "Waldzustandserfassung" des Landes SUdtirol an 6 FreiflachenmeBstellen wet only- und bulk- Niederschlagsmessungen

durchgefUhrt . In den wochentlich

eingesammelten Niederschlagsproben wird, neben dem pH-Wert und der elektrolytischen Leitfahigkeit, vor allem der Gehalt an saurebildenden Anionen (Sulfat, Nitrat und Chlorid) untersucht . An den emi ttentenfernen MeBstellen liegt der mengengewichtete Jahresmittelwert (bulk) wahrend des MeBzeitraumes 1983 bis 1987 fUr pH zwischen 4 . 72 und 5 . 15, ftir S04-S zwischen O . 51 und 0 . 89 (mg/1), fUr N03-N zwischen 0 . 25 und 0 . 51, fUr NH4-N zwischen O . 29 und O . 58 und fUr Cl zwischen 0 . 2 und 0 . 5 ; der Jahreseintrag (bulk)

von S04-S betragt 0 . 32 - O, 75 (g/m² *a), von N03-N 0 . 21 - 0 . 39, von NH4-N 0 . 25 - 0 . 56 und von Cl 0 . 13 - 0 . 55 .

SUMMARY

Joining a local forests damages surveying project, rain water analysis (wet only and bulk) have been performed on samples collected on six different stations in South Tirol since 1983 . The samples were collected once a week, pH and conductivity were measured and chemical analysis performed, particularly the determination of the acid-building anions

(sulphate, nitrate and cloride) .

The samples collected on the stations located far from the sources of emissions show in the period 1983-1987 annual quantity-weighted means for pH between 4,72 and 5,15, for sulphate between 0, 51 and 0, 89 mg S /1, for nitrate between 0,25 and 0,51 mgN/1, for ammonium between O, 29 and 0, 58 mgN/1 and ·-ror cloride between 0,2 and 0,5 mg/1 .

LITERATUR

Bendetta, G . 1988. Umweltbelastungen durch Luftverschmutzung in SUdtirol . In : Oko­

physiologische Probleme durch Luftverun­

reinigungen . Hsg . Grill, D . & H . Gutten­

berger . 73-81 . Institut fUr Pflanzenphysio­

logie der Universitat Graz .

Egner, H . und E . Eriksson . 1955 . Current Data on the Chemical Composition of Air and Precipitation . Tellus, 7 : 134 .

Landesforstdirektion Tirol . 1988. Zustand der Tiroler Walder . Bericht an den Tiroler Landtag .

Smidt, S . 1984 . Analysen von Niederschlags­

proben aus Waldgebieten Osterreichs . Allg . Forstztg . , H . 1 : 13-15 .

Likens, G . E . 1988. Acid rain and its effects on sediments in lakes and streams . Proc.

4th Int . Symp . on The Interaction Between Sediments And Water . Melbourne, Australia.

Feb . 16-20 .

Moselle, R . , Tartari, G . & G . A . Tartari . 1985 . Chemistry of bulk deposition at Pallanza during the decade 1975-1984 . Mem . Ist . Ital . Idrobiol . 43 : 311-332 .

Soderland, R . 1982 . On the difference in chemical composition of precipitation collected in bulk and wet-only collectors . Report CM-57 . Department of Meteorology, University of Stockholm .

Gruppo di Studio, 1987 . Deposizioni Atmos­

feriche nel Nord Italia. Rapporto finale . anni 1983-1984 . Ingegneria Ambientale, 6 : 1-63 .